3.0 affected environment and...
TRANSCRIPT
Davy Crockett NF – Lancaster-Forsythe Project
Environmental Assessment Phase I – Compartment 113 & 114 – Crib & Forsythe Creek
Chapter 3. Alternatives, Including the Proposed Action Page 1 of 52
This section summarizes the key
environmental impacts of the two alternatives.
It provides the necessary information to
determine whether or not to prepare an
Environmental Impact Statement. The
analysis that follows has considered the best
available science when evaluating the impacts
of the proposed project on the forest resources
through a review of scientific literature, a
consideration of responsible opposing views,
and the acknowledgement of incomplete or
unavailable information, scientific
uncertainty, and risk. This includes reports
submitted by Forest Service Specialists that
are in the project file.
3.1 Soil
3.1.1 Affected Environment According to the Ecological Classification
System for the National Forests of the West
Gulf Coastal Plain, this project lies within the
Clayey Uplands Landtype Association. The
Clayey Uplands LTA occurs on the slightly
rolling terrain of the Cook Mountain, Yegue,
Yazoo, Moodys Branch, and Caddell
formations. The Cook Mountain formation
consists of marine and littoral, clay, and
glauconite. The Yegua formation consists of
continental and palustrine sand and sandy
clay. The Yazoo, Moodys Branch, and
Caddell formations consist of marine clay and
glauconitic sands and marl. Clayey soils with
small amounts of loamy topsoil are common.
Pre-settlement vegetation was probably
variable, and included beech-white oak,
loblolly pine-oak, shortleaf pine-oak, and
longleaf pine-little bluestem communities.
The Clayey Uplands occupies most of the
Davy Crockett National Forest.
The Natural Resource Conservation Service
(NRCS) has completed an Order II Soil
Resource Inventory for the Davy Crockett
National Forest. This soil survey has more
detailed information on the soils and their
suitability for the existing conditions and
proposed actions than the Ecological
Classification System. Detailed analysis for
soil and water effects was performed using
the NRCS soils information. The Lancaster-
Forsythe Project lies over several different
soil series; some of the more predominant
soils include Fuller, Moswell, Latex, Keltys,
and Penning.
The Fuller Soil Series consists of very deep,
somewhat poorly drained, nearly level and
gently sloping soils on uplands. Formed from
loamy sediments over mudstone, they have a
fine sandy loam surface layer. Subsoil for
this series is a silty clay loam.
The Latex Soil Series consists of very deep,
moderately well drained, slowly permeable
soils that formed in loamy sediments over
clayey deposits on uplands. The soil has a
fine sandy loam surface texture, with clay
loam subsoil.
The Moswell Soil Series consists of deep,
well- drained, gently sloping to moderately
steep soils on uplands. They have a loamy
surface texture with dense clay subsoil.
The Keltys Soil Series consists of very deep,
very gently sloping to moderately sloping,
slowly permeable, moderately well drained
soils on uplands. The surface layer is fine
sandy loam with a fine sandy loam subsoil.
3.0 Affected Environment
and Environmental
Consequences
Davy Crockett NF – Lancaster-Forsythe Project
Environmental Assessment Phase I – Compartment 113 & 114 – Crib & Forsythe Creek
Chapter 3. Alternatives, Including the Proposed Action Page 2 of 52
The Penning Soil Series consists of deep,
moderately well drained, moderately
permeable soils. Formed in loamy alluvium
over shale, the surface layer is very fine sandy
loam, with very fine sandy loam subsoil.
Other soils included in the area include the
Moten-Multey complex – a deep, moderately
well drained upland fine sandy loam; the
Alazan soil series of loamy alluvial sediments
found on stream terraces; the Kurth soil series
of moderately well drained fine sandy loams
found on the uplands, as well as several
others, displayed in Table 3-1 (USDA-NRCS,
2009a). Maps showing soil locations are in
Appendix A.
Table 3-1. Soil Characteristics in Compartment 113 & 114
Map Unit
Soil Name Harvest Equipment Operability
1
Potential Erosion Hazard (Off-
Road/Off-Trail)2
Potential Fire Damage Hazard
3
AaB Alazan very fine sandy loam, 0-2% slopes
Moderate** Slight* Low*
EtB Etoile loam, 1-3% slopes Moderate Slight Moderate
FuB Fuller fine sandy loam, 1-3% slopes
Moderate Slight Low
KeB Keltys fine sandy loam, 1-3% slopes
Moderate Slight Moderate
KoA Koury silt loam, 0-1% slopes, frequently flooded
Well-suited* Slight Moderate
KuB Kurth fine sandy loam, 1-3% slopes
Well-suited Slight Moderate
LdB Latex fine sandy loam, 1-3% slopes
Moderate Slight Moderate
MsB Moswell loam, 1-5% slopes Moderate Slight Moderate
MsD Moswell loam, 5-15% slopes Moderate Moderate Moderate
MxA Moten-Multey Complex, 0-2% slopes
Moderate Slight Low
PeB Penning very fine sandy loam, 0-2% slopes
Moderate Slight Low
PoA Pophers silty clay loam, 0-1% slopes, frequently flooded
Moderate Slight Low
UrB Urland fine sandy loam, 1-5% slopes
Well-suited Slight Moderate
The suitability for operation harvesting equipment. Rating assessment: The off-road transport or harvest of logs and/or wood
products by ground-based wheeled or tracked equipment. The use of standard rubber-tired skidders and bulldozers used for
ground-based harvesting and transport.
1. Ratings indicate the hazard or risk of soil loss from off-road and off-trail areas after disturbance activities that expose the
soil surface. This includes sheet and rill erosion from exposed soil surfaces caused by various silvicultural practices,
grazing, mining, fire, firebreaks, etc.
2. The potential hazard of damage to soil nutrient, physical, and biotic characteristics from fire. Rating assessment: The
impact of fires (prescribed or wildfire) of moderate fireline intensity (116-520 btu’s/sec/ft) that provide the necessary heat to
remove the duff layer and consume soil organic matter in the surface layer.
* Slight, low, or well-suited - Presents, at most, minor problems for the specified use. The soil gives satisfactory
performance with little or no modification. Modifications or operations dictated by the use are simple and relatively
inexpensive. With normal maintenance, performance should be satisfactory for a period of time generally considered
acceptable for the use.
** Moderate or moderately suited - Does not require exceptional risk or cost for the specified use, but the soil
does have certain undesirable properties or features. Some modification of the soil itself, special designs, or
Davy Crockett NF – Lancaster-Forsythe Project
Environmental Assessment Phase I – Compartment 113 & 114 – Crib & Forsythe Creek
Chapter 3. Alternatives, Including the Proposed Action Page 3 of 52
maintenance are required for satisfactory performance over an acceptable period of time. The needed measures
usually increase the cost of establishing or maintaining the use, but the added cost is generally not prohibitive.
*** Severe or high - Requires unacceptable risk to use the soil if not appreciably modified. Special design, a
significant increase in construction cost, or an appreciably higher maintenance cost is required for satisfactory
performance over an acceptable period of time. A limitation that requires removal and replacement of the soil would
be rated severe. The rating does not imply that the soil cannot be adapted to a particular use, but rather that the cost
of overcoming the limitation would be high (http://soils.usda.gov/technical/manual/print_version/chapter6.html;
accessed March 20, 2008)
Cumulative Effects
The boundaries for Compartments 113, and
114 define the cumulative effects area (CMA)
for soils. Activities that have occurred in
these compartments in the last three years
(2007-2009) will be considered, since this is
the amount of time it takes for an area to
recover from disturbances such as timber
harvesting (See Table 3-2). Activities
planned for the next ten years (2010-2020) in
these two compartments will also be
considered, as projects included in this
document may be implemented over the
course of ten years.
Table 3-2 - Activities that have taken place in CEA
Compt. Action
113 243 acres thinned in 2009
814 acres prescribed burned in 2008
1,707 acres prescribed burned in 2006
134 acres of midstory reduction in
2008
114 2,014 acres prescribed burn in 2009
2,014 acres prescribed burn in 2007
290 acres of midstory reduction 2008
Occasional road maintenance is the only other
activity that has taken place during the last
three years.
Private Land – One block of private land,
approximately 100 acres, lies within the
cumulative effects area, in C-113. This block
consists mainly of pasture.
3.1.2 Environmental Consequences
3.1.2.1 Alternative 1 (No Action)
In implementing this alternative, no additional
activities would occur to impact soil
properties. Conditions would generally
remain the same. Changes to soil properties
would be the result of natural disturbances,
such as windstorms or wildfire. A windstorm
could uproot trees and expose soils.
Similarly, wildfire could kill overstory
vegetation, expose soil, and result in soil
nutrient losses and erosion. These events,
however, are rare and the overall risk to soil
resources from natural events is low.
The NRCS Soil Inventory discloses the
potential fire damage hazard, which reflects
the potential for damage to soil nutrients,
physical, and biotic characteristics from fire.
Ratings assess the impact of fires, prescribed
or wildfire, of moderate intensity (116-520
btus/sec/ft) that provide the necessary heat to
remove the duff layer and consume soil
organic matter in the surface layer.
Some areas in Compartment 113 have a
severe potential fire damage hazard. Most
likely, the no action alternative would result
in a greater probability of soil damage to
these areas, assuming that this compartment
could eventually be burned by a wildfire
under moderate to extreme weather
conditions.
Under this alternative, no roads would be
blocked by gates or berms; wing ditches and
culverts would not be rehabbed, and erosion
Davy Crockett NF – Lancaster-Forsythe Project
Environmental Assessment Phase I – Compartment 113 & 114 – Crib & Forsythe Creek
Chapter 3. Alternatives, Including the Proposed Action Page 4 of 52
and sedimentation would continue at the
present rates on all the roads in Compartments
113 & 114.
Cumulative Effects
Under this alternative, the greatest potential
for cumulative impacts to soils in the
Lancaster-Forsythe Project, Phase I would be
the continued erosion along roads from
improperly designed and functioning
drainage.
3.1.2.2 Alternative 2
Approximately 2,351 acres would be
disturbed by harvest activities. Thinning
could cause compaction in the skid trails,
landings, and on the temporary roads. The
amount of compaction that would occur is a
function of the volume being removed per
acre, the number of acres being harvested, the
logging equipment used by the timber
purchaser, and soil moisture conditions.
Mitigation measures to limit the operating
period during wet conditions would help
protect these soils. One compaction study
found that compaction has little to no effect
on early pine productivity. Eighty percent of
soil compaction occurs after one pass by
heavy equipment, and no differences can be
found after four passes. Recovery from
compaction depends on the soils, degree of
compaction, and type of vegetation present.
(Scott, et. al 2004).
The removal of trees could increase the
potential for erosion from an increase in run
off caused by reducing the soil cover.
Limiting operations to dry periods and the
relatively infrequent entries into the stands
provide adequate protection of soil by
limiting soil movement and compaction.
Harvested stands would maintain a tree
canopy, resulting in a moderate potential from
soil movement. The soils would have time to
recover from the effects of compaction prior
to the next timber harvest (USDA 1989).
The Plan contains coefficients to estimate
potential soil erosion for the general soil types
in the areas where activities are planned. The
regeneration in the storm damage areas in
Compartments 113, Stands 88 and 89;
Compartment 114, Stand 89 are at or exceed
acceptable levels of stocking. Thinning
would potentially increase erosion to 0.07
tons per acre per year, well under the
tolerance level of 4.8 tons per acre per year.
Tolerance levels provide an estimate of the
total soil loss that can be allowed from
accelerated erosion without substantially or
permanently lowering soil productivity (The
Plan, Appendix F).
Prescribe burning on the proposed cycle
would allow litter-duff biota to fully recover
between burns. Physical soil properties
would not be affected. Underburns do not
cause significant leaching losses because
nutrients would be retained through the
uptake by unburned plants. Loss of organic
matter would be about five percent.
Underburns are usually light to moderate in
severity and expose little or no soil, so their
effect on erosion is generally negligble.
Overall risks to soil productivity from
underburns are minimal (USDA 1989).
To minimize the potential for effects on soil
resources, firelines will not be constructed
near stream course zones. Existing barriers
such as roads, streams, and permanent fire
lines are used whenever possible to minimize
fire line construction. Bladed lines are
constructed/reconstructed as opposed to
plowed, in order to minimize soil resource
damage. Water diversion structures and
prompt revegetation on constructed control
lines would prevent soil loss. Post-burn
monitoring determines the need for follow-up
Davy Crockett NF – Lancaster-Forsythe Project
Environmental Assessment Phase I – Compartment 113 & 114 – Crib & Forsythe Creek
Chapter 3. Alternatives, Including the Proposed Action Page 5 of 52
implementation of additional erosion control
measures. The same firelines are used for
repeated burns.
Prescribed burning under Alternative 2 would
be within acceptable limits on areas with
severe potential fire damage hazard, because
weather and fuels would be optimum,
minimizing damage.
The effects of mechanical midstory control
(mulching) are similar to those associated
with chopping and mowing, which rarely
cause compaction. Most vegetation would be
cut above the ground line, so little soil would
be disturbed. Overall risks to soil
productivity and nutrient displacement from
this type of midstory control would be
minimal (USDA 1989).
It is generally accepted that the majority of
sediment produced by forest management
practices comes from forest roads (Gucinski,
et. al. 2001). Although road improvements
would disturb soil, the work that will be done
is designed to improve the stability of road
surfaces and improve drainage of the roads.
These activities would, in the long term,
decrease the amount of sediment produced by
the road system.
The construction of temporary roads would
create the potential for soil movement. Initial
ground disturbance produces the greatest
sediment yield (Blackburn et. al. 1989).
Following the timber sale, temporary roads
will be obliterated, seeded, water bars
installed and entrances blocked. The closing
of most low standard system roads and illegal
roads will promote vegetative cover and
reduce surface runoff. Blocking maintenance
Level 1 and 2 roads would eliminate a
substantial source of sediment due to run-off.
Alternative 2 proposes using the herbicide
triclopyr to control NNIPS if monitoring
shows that the need exists. Triclopyr applied
at the typical rate allowed in forest
management (about one pound per acre of
active ingredient) would be readily degraded
by both chemical and biological mechanisms,
primarily photodegradation and microbial
decomposition, respectively. Application
methods would kill unwanted vegetation but
would leave the plant residue and root
systems in place, intercepting rainfall and
reducing erosion potential (Michael et. al
2000).
The application of the herbicide triclopyr in
the treatments proposed in this EA would be
to targeted species and applied by hand, thus
minimizing effects to surface or ground water.
triclopyr has little or no soil activity. triclopyr
degrades rapidly in the soil mostly by
photodecomposition but also by microbes. Its
half-life in the soil varies from 3.7 to 314
days but averages 30 days (Tu et. al. 2001).
triclopyr has low leaching characteristics
though leaching depends on soil pH and
organic matter; more leaching occurring in
light soil and heavy rainfall.
Herbicides do not disturb soil, so treated areas
usually have intact litter and duff that
eliminate or at least minimize erosion.
(Michael et. al. 2000) The impact to soil
biota is negligible at typical rates. Due to type
of application, little soil activity, rapid
degradation, and low rate of application, no
adverse effect would be expected to soil from
the use of herbicides.
Cumulative Effects
The cumulative effects to soils from activities
proposed in Alternative 2, would result in
some risks to soil productivity, mainly
through nutrient displacement and erosion.
Davy Crockett NF – Lancaster-Forsythe Project
Environmental Assessment Phase I – Compartment 113 & 114 – Crib & Forsythe Creek
Chapter 3. Alternatives, Including the Proposed Action Page 6 of 52
Road construction and improvements needed
to access the harvest areas present the greatest
potential for both nutrient displacement and
soil erosion in the cumulative effects area.
All roads would be constructed or improved
to The Plan’s standards and guidelines.
These measures minimize the potential for
erosion.
The timber harvest activities would be
implemented over a period of several years.
Ground disturbance would not be
concentrated in any one area during any time
period at levels that would result in significant
cumulative effects.
3.2 Water
3.2.1 Affected Environment
Several major stream systems drain the
Lancaster-Forsythe Project, Phase I. North
and Crib Creeks flow out of compartments
112 and 113 and Forsythe Creek drains
compartment 114. All of these streams flow
into the Neches River.
Stream courses within the Lancaster-Forsythe
Project, Phase I exhibit characteristics
common to most streams in the East Texas
region. Some intermittent and ephemeral
tributaries of the main streams show
successional head cutting of the stream
channel. This condition is believed to have
been initiated when the area was cutover in
the 1930’s. The successional head cutting
will continue until the channel reaches the
natural angle of repose. The Lancaster-
Forsythe Project, Phase I contains an
extensive road network and 15-18 percent of
these two watersheds consists of non-
woodlands (mainly pasture) which has a
higher run-off than area with a mature stand
of timber. The primary beneficial uses of the
streams in the project area are fisheries and
recreation.
The NRCS Order II Soil Resource Inventory
identifies the Koury and Pophers soil series as
flood plain soils. Wetlands may be associated
with these areas; however, either flood plains
or wetlands have been identified on the
ground.
Cumulative Effects
The cumulative effects area for water consists
of the two watersheds for North and Crib
Creeks, and Lancaster and Forsythe Creeks,
totaling 16,280 acres. A map of these
watersheds is located in the project file.
Table 3-3, below displays the details of each
watershed.
Table 3-3 - Watersheds in Cum. Effects Area
Watershed NF acres
Pvt acres
Total Area
North/Crib Creeks 4,501 4,939 9,440
Lancaster/Forsythe Creeks
4,790 2,050 6,840
Activities that have occurred, or will occur, in
these watersheds between 2010 and 2020 will
be considered in the cumulative effects to
water for this project. Activities that have
occurred in compartments 113 - 114 are listed
in Table 3-2.
Private Land – As shown in Table 3-3, 42
percent of the cumulative effects area for
water is privately owned. Nearly 60 percent
of the private land within the two watersheds
is forested; the remainder is in pasture.
3.2.2 Environmental Consequences
3.2.2.1 Alternative 1 (No Action)
No additional management-initiated impacts
to water would occur under this alternative.
Conditions would generally remain the same.
Changes to water properties would result
mainly from natural disturbances, such as
windstorms or wildlfire. These events,
Davy Crockett NF – Lancaster-Forsythe Project
Environmental Assessment Phase I – Compartment 113 & 114 – Crib & Forsythe Creek
Chapter 3. Alternatives, Including the Proposed Action Page 7 of 52
however, are rare and the overall risk to water
resources from natural events is low.
Cumulative Effects
While no activities would take place in
Compartments 113 and 114, under this
alternative, actions in other compartments in
this watershed would still go forward.
Prescribe burning is planned for the
surrounding compartments on a 2 to 3 year
cycle.
The biggest cumulative impact to water in the
two watersheds surrounding the Lancaster-
Forsythe Project, even with the ongoing
activities listed above, would be the continued
sedimentation from the roads.
3.2.2.2 Alternative 2
Water yields will increase temporarily after
harvesting and prescribed burning are
implemented. This effect is more related to
reduced water use by vegetation than effects
on soil properties (USDA 1989 and
Blackburn 1989). Surface runoff could cause
erosion where water becomes channeled and
mineral soils are exposed. Skid trail and
temporary roads would produce most of the
soil movement. Establishment of stream
protection zones, waterbarring, seeding, and
fertilizing of bare soil areas would mitigate
the potential for sediment delivery to streams.
Underburns have a negligible effect on stream
nutrients, water yields, and stream sediment
loads (USDA 1989). To minimize the
potential for effects on soil and water
resources, firelines would not be plowed near
stream course zones. Water diversion
structures and prompt revegetation would
prevent soil loss and sedimentation in stream
courses.
Road improvements would disturb soil, but
they are designed to improve the stability of
road surfaces and improve drainage of the
roads. In the long-term, the amount of
sediment produced by the road system would
be reduced. System road and temporary road
construction would create the potential for
soil movement. Skid trails and temporary
roads will produce most of the sediment
resulting from logging activities. Initial
ground disturbance produces the greatest
sediment yield (Blackburn et. al. 1989).
Sediment production from Coastal Plains
forest roads having little or no slope can be
dramatically reduced through road
management practices (Appelboom et. al.
2002). Following the timber sale, temporary
roads will be obliterated, seeded, water bars
installed and entrances blocked. The closing
of most low standard system roads will
promote vegetative cover and reduce surface
runoff. Blocking system roads by gating or
berming would eliminate them as a source of
sediment and return them to productivity.
The Roads Analysis Report for the Lancaster-
Forsythe Project documents that some roads
have altered drainage patterns in the project
area. These roads were originally designed to
minimize potential erosion through the
installation of wing ditches and cross drain
culverts. However, wing ditches have
concentrated water into the wing ditches,
resulting in runoff reaching stream channels.
The Roads Analysis Report also recommends
site specific ways to improve the roads which
will also decrease erosion and sedimentation.
Alternative 2 proposes using the herbicide
triclopyr to control NNIPS if monitoring
shows that the need exists. The analysis of
herbicides on water properties in the Final
Environmental Impact Statement for
Vegetation Management in the Coastal
Plain/Piedmont describes negligible effects of
triclopyr on surface water, ground water,
stream nutrients, and stormflows. The
Davy Crockett NF – Lancaster-Forsythe Project
Environmental Assessment Phase I – Compartment 113 & 114 – Crib & Forsythe Creek
Chapter 3. Alternatives, Including the Proposed Action Page 8 of 52
potential for effects on water would arise
from application directly into a stream,
application drift to water from adjacent areas,
or off-site movement from treated areas in the
soil (USDA 1989). A more recent study came
to a similar conclusion: movement of
triclopyr through surface and subsurface
runoff in areas with minimal rainfall is
believed to be negligible (Tu et. al. 2001).
On site degradation processes and in-stream
dilutions and degradation result in quick
dissipation of herbicide residues. Short-term
water quality effects are minimal, and long-
term water quality is not adversely affected.
Long-term water quality can be improved by
herbicide use since stream sedimentation is
reduced (SERA 2003 and Michael et. al.
2000). The management requirements to
establish protection zones, the use of selective
hand application methods, and the physical
and chemical properties of triclopyr would
minimize the risk.
Triclopyr has a half-life in water of 10 hours
at 77degrees F. The Plan requires that no
herbicide be ground-applied within 30
horizontal feet of lakes, wetlands, or perennial
or intermittent springs or streams. Project
design criterion #17 states that “no herbicides
will be applied within MA-4 or within 33 feet
of ephemeral streams (Ch 2, Specific Design
Criteria to Alternative 2, p. 5). These
requirements will contribute to the protection
of the soil and water resources. Due to type
of application, little soil activity, rapid
degradation, and low rate of application, no
adverse effect would be expected to water
from the use of herbicides.
Cumulative Effects
Thinning, midstory reduction and prescribed
burning in Compartments 113 and 114; and
road maintenance are the activities that have
occurred in the cumulative effects area in the
last three years on National Forest, in the four
watersheds that surround the project area.
The cumulative effects to water from these
activities, combined with those proposed
under the Proposed Action, would result in
some risks to water quality, mainly through
sedimentation.
Road construction and improvements needed
to access the harvest areas proposed in the
Proposed Action present the greatest potential
for watershed effects in the project area. All
roads would be constructed to The Plan’s
standards and guidelines. These measures
minimize the potential for stream
sedimentation.
The timber harvest activities would be
implemented over a period of several years.
Not all of the area would be harvested in any
one year and it is probable that timber
harvesting would be spread over the next five
to seven years under the Proposed Action.
Ground disturbance would not be
concentrated in any one area during any time
period at levels that would result in significant
cumulative effects. No management activities
that would affect water resources are expected
on the private land in the area.
3.3 Air
3.3.1 Affected Environment
The Forest Objective is to meet the National
Ambient Air Quality Standards (NAAQS) as
defined by the amended Clean Air Act. The
Davy Crockett NF is considered to be in
attainment of the National Ambient Air
Quality Standards (NAAQS) for Class II air
sheds. The nearest non-attainment area is in
Montgomery County, approximately 60 miles
south of Compartment 113 and114.
Montgomery County lies within the
Houston/Galveston, TX non-attainment area.
The air quality within Trinity County, where
Davy Crockett NF – Lancaster-Forsythe Project
Environmental Assessment Phase I – Compartment 113 & 114 – Crib & Forsythe Creek
Chapter 3. Alternatives, Including the Proposed Action Page 9 of 52
the project is located, is generally good, but
regional haze affects visibility in the area
year-round, especially during the summer
months.
Cumulative Effects
The Cumulative Effects Area for air includes
Trinity County, in which Compartment 113
and 114 lie. Most states monitor air quality
in this manner, on a county basis. Since
prescribed fire is the only vegetation
management method that emits substantial
amounts of gases and particulates to the
atmosphere, prescribed burning that has
occurred in 2010 will be the main activity to
be considered for cumulative effects (USDA
1989). The Davy Crockett NF completed
about 19,180 acres of prescribed burning in
2010, in Trinity County.
3.3.2 Environmental Consequences
3.3.2.1 Alternative 1 (No Action)
Under this alternative, impacts to air quality
would be limited to naturally occurring
processes.
Cumulative Effects
Cumulative effects to air would be negligible
under this alternative.
3.3.2.2 Alternative 2
Prescribed fire generates several pollutants,
two of which are of the biggest concern to
Forest Service fire managers: particulate
matter and ozone. State air quality
monitoring data indicates that Trinity County
is in attainment for fine particulate matter at
this time. Monitoring data for ozone
collected near the Davy Crockett NF indicates
that current conditions of ozone pollution are
acceptable in terms of NAAQS. Prescribed
fire should be considered only as a small
source of particulate matter or ozone
pollution. Weather and climate in Texas
preclude prescribed fire from becoming a
contributor to ozone non-attainment (USDA
2003).
The major local effects of prescribed burning
are visibility reduction and respiratory
impairment. These effects are expected to be
brief, intermittant, and confined to time of
burning (USDA 1989).
The Forest Service mitigates prescribed
burning air quality effects by conducting
burns during appropriate weather conditions
and using proper ignition and smoke
management tools. Because of this, no effects
regarding attainment of state air quality
standards should be expected. The Air
Quality Report includes a more detailed
discussion of prescribed burning and its
effects on air (included in the Project File).
Parameters that will be followed to mitigate
the impacts of smoke: Table 3-4
Wind speed > 6 mph
Relative humidity > 20 %
Transport winds > 4 m/s
10-hour fuel moisture > 7 % @ weather station
Mixing height > 500 m
Wind direction Carry smoke away from
sensitive target
Cumulative Effects
Cumulative effects to air quality under this
alternative would be negligible. State air
quality monitoring data shows that the Davy
Crockett NF is in attainment at this time.
Weather and climate conditions in Texas
preclude prescribed fire from becoming a
contributor to ozone non-attainment (USDA
2003).
Since it is likely that the Texas Commission
on Environmental Quality will allow the
Forest Service to use prescribed fire
elsewhere on the Davy Crockett NF,
Davy Crockett NF – Lancaster-Forsythe Project
Environmental Assessment Phase I – Compartment 113 & 114 – Crib & Forsythe Creek
Chapter 3. Alternatives, Including the Proposed Action Page 10 of 52
essentially no differences exist between the
current conditions and Alternative 2 in terms
of expected annual emissions.
3.4 Recreation and Scenic Resources
3.4.1 Affected Environment
Recreation
The Davy Crockett Ranger District lies about
120 miles north of the Houston metropolitan
area. Recreation use in Compartment 113 and
114 consists primarily of hunting. The
Lancaster-Forsythe Project Area is part of the
Alabama Creek Wildlife Management Area
and is managed cooperatively with Texas
Parks and Wildlife Department (TPWD). The
common goal is to develop and manage
wildlife resources on the Davy Crockett
National Forest. Deer and turkey hunting are
the primary focus of TPWD management
activities. Dispersed camping, hiking, and
bird-watching are other possible activities that
could take place in these compartments.
Scenic Resources
Most of Compartments 113 and 114 have a
visual quality objective (VQO) of maximum
modification. Maximum modification allows
management activities, such as vegetative and
landform alterations, to dominate the
landscape.
Management Area 2 (MA-2) (red-cockaded
woodpecker emphasis) in Phase 1 has a visual
quality objective (VQO) of maximum
modification. In maximum modification, the
management activities may be dominant, but
appear as natural when viewed as
background. Management activities can also
be out of character when viewed as
foreground and middleground. The more
sensitive area of MA-4 (streamside
management zones) and the predominantly
used travel way, FM 357, have a VQO of
partial retention. Management activities in
partial retention may be visible but should
remain subordinate to the character of the
surrounding landscape. Forest Service
System Road 531 and 541 have a VQO of
modification. Management activities in
modification may be dominant features, but
are of an appropriate scale and form so as to
appear as a natural occurrence within the
surrounding area.
The majority of the land along the travel
ways, within the project area, is forested.
There is some private land with open, field
views. The feeling of openness, or tightness,
changes depending on the type of roadway
one is traveling. For example: along FM 357
the tree lines are set back from the edge of
pavement. While forested on both sides, the
wide expanse between the tree lines provides
more openness. The roadway undulates over
gently rolling slopes, providing a pleasant
setting. Forest Service System Roads 531and
541 evoke a different setting. The roadways
are narrower, the tree lines are closer to the
edge of the road and one feels more enclosed
within the corridor.
The 1996 Revised Land and Resource
Management Plan for the National Forests
and Grasslands in Texas (The Plan) describes
the desired future condition of MA-2
generally as open pine forest mixed with
some hardwoods with the primary
management goal of improving the habitat for
the red-cockaded woodpecker (RCW). To
achieve this goal, the management activities
require frequent fire to create an open, grass
understory. Timber management activities
are evident throughout due to the focus on
management and restoration of upland pine
forest with large older pine trees to provide
the best opportunity for RCW habitat. MA-4
is generally described as streamside
management zones with bottomland
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Chapter 3. Alternatives, Including the Proposed Action Page 11 of 52
hardwoods. MA-4 is not managed for timber,
but fire may be used for enhancement.
Cumulative Effects Area
The cumulative effects to visual quality
would be minimal in that C-113 and 114
would retain their overall forested character.
Initial effects of management activities would
be temporary and, where necessary, mitigated
to reduce the impact to the visual resources.
The actions proposed would result in changes
to the scenery by opening the many layers of
the forest (understory, midstory, overstory).
3.4.2 Environmental Consequences
3.4.2.1 Alternative 1 (No Action)
Under the No Action alternative, the views
along the roads would remain as they are for
some time. The stands that currently are open
along the road side would begin to fill in with
vegetation and existing views into the forest
would begin to close. As pine stands within
the project area decline with age, the under
story would become denser and middleground
views along the roadways would revert to
primarily foreground. With a lack of
management activities, the possibility of rapid
change is increased due to natural events such
as wildfire, straight-line winds and insects
(such as the SPB outbreak in the 1980’s).
These events can have devastating effects on
the quality of the scenery, as is evident by the
windstorm-damaged areas within this project
area. The pine plantations would have
difficulty developing into healthy trees and
would be more susceptible to insects.
Cumulative Effects
The cumulative effects to the quality of the
visual landscape would change. The
compartments would retain their overall
forested character while the views into the
compartments, from the roadside corridors,
would all become primarily short distant
foreground views.
3.4.2.2 Alternative 2
The proposed management activities of
thinning, midstory removal, and burning
would have an effect on both compartments
including approximately 11 miles of road
frontage. The proposed management
activities would keep existing views open and
provide longer distance views into areas that
currently are foreground only, creating visual
depth into the forested land. Along FM 357
and NFSR 531 and 541 a combination of
activities would occur. Evidence of burning
would be noticeable along the road sides.
Thinning pine plantations would continue the
process of opening the stands which would
allow the remaining trees to become larger
with better shaped canopy. Thinning in the
mature pine stands would create a more open
park-like feeling. Midstory removal, where
necessary, would also add to the open park-
like views. To obtain the desired future
conditions, and therefore increase the
middleground views, continued burning is
necessary. Burning the pine stands would
provide the open grass-like understory, which
also increases visibility.
Initially, there would be locations where the
difference between existing views and the
views after management activities would be
very dramatic. To provide a transition
between travel ways and management
activities, design criteria have been
developed. In locations identified as partial
retention, felling cuts are to be directed away
from the specified roadways and stream sides
within a 200 foot lop and scatter zone.
Additionally, within the zone, visible slash is
to be lopped to lie within 2 feet of the ground,
chipped or removed. Log decks are to be out
of sight, where possible. If leave trees are to
be marked it should not visible from the
travelway or streamside. Along travelways
identified as modification the felling cuts are
to be directed away from the travelways. The
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Chapter 3. Alternatives, Including the Proposed Action Page 12 of 52
lop and scatter zone remains 200 feet,
however, the lop to lie within 2 feet zone shall
be 100 feet. Log landings are to be a
minimum of 300 feet from the travelway. As
in partial retention, leave trees are to be
marked so as not seen from the travelway.
Current logging techniques will create some
openings along the roads in the thinned
stands, but longer middleground views would
be created when the stands are regularly
burned. When burned, scorch and bark char
would be visible for sometime; however, this
is a natural part of fire. After several
rotations of fire have reduced the fuels, fire
would be less intense and scorch and bark
char would be less visible.
Cumulative Effects
The cumulative effects to visual quality
would be minimal in that C-113 and 114
would retain their overall forested character.
Initial effects of management activities would
be temporary and, where necessary, mitigated
to reduce the impact to the visual resources.
The actions proposed would result in changes
to the scenery by opening the many layers of
the forest (understory, midstory, overstory).
3.5 Heritage Resources
3.5.1 Affected Environment
The Heritage staff reviewed the proposed
activities for the Groveton Fuels Reduction
Project and found that the proposed activities,
such as thinning and prescribe burning, would
not adversely affect any Historic Properties as
defined in 36 CFR 800. A Heritage
Management Summary detailing this finding
of “no adverse effect” has been submitted to
the Texas Historic Preservation Office
(SHPO) and other interested parties.
Documentation certifying SHPO concurrence
with the findings of the Heritage Management
Summary has been received.
Cumulative Effects
The cumulative effects area for heritage
resources consists of Compartments 113 and
114.
3.6 Vegetation and Fuels
3.6.1 Affected Environment
Vegetation
The Lancaster-Forsythe Project, Phase I
encompasses approximately 3,721 acres of
the Davy Crockett NF. All of Compartments
113 and 114 (3,721 acres) fall within
Management Area 2 (MA-2), Red-Cockaded
Woodpecker (RCW) Emphasis, while about
224 acres consist of streamside management
zones (MA-4), primarily Forsythe and Crib
Creeks and intermittent streams feeding them.
Upland Vegetation (MA-2)
Species composition – Loblolly pine (Pinus
taeda) and shortleaf pine (Pinus echinata)
dominate most of the stands in the Lancaster-
Forsythe Project, interspersed with a mixture
of hardwoods. Several stands are dominated
by shortleaf pine. Hardwood tree species
common to the overstory in these stands
include white oak (Quercus alba), southern
red oak (Q. falcata), post oak (Q. stallata),
sweetgum (Liquidambar styracuflua), hickory
(Carya sp.), and ash (Fraxinus sp.).
Structure – The even-aged pine forest
communities in the Lancaster-Forsythe
Project contain three layers – overstory,
midstory, and understory. The midstory and
understory vegetation and densities are typical
of those found in the East Texas Pineywoods
and consist primarily of oaks (Quercus), pines
(Pinus), hickories (Carya), elms (Ulmus sp.),
ironwood (Ostrya virginiana), blackgum
(Nyssa sylvatica), sweetgum, dogwood
(Cornus florida), cherry (Prunus sp.), red
maple (Acer rubrum), magnolia (Magnolia
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Chapter 3. Alternatives, Including the Proposed Action Page 13 of 52
sp.), mulberry (Morus rubra), hawthorn
(Crataegus sp.), and chinquapin (Castanea
pumila). The understory consists of yaupon
(Ilex vomitoria), Carolina buckthorn
(Rhamnus caroliniana), and vines as well as
seedlings and saplings of the species found in
the midstory and overstory. Grasses and
other herbaceous vegetation are also typical
of forests in East Texas.
About 33 percent (785 acres) of these pine
forest communities are less than 36 years old,
following natural disturbances such as SPB
infestations and windstorms, as well as some
planned regeneration.
In November 2004, a tornado blew down
several hundred acres of pine and hardwood
trees in the total Lancaster-Forsythe Project
Area. (Compartments 113 and 114 were
affected by this weather event). Blown
down trees, trees with tops broken out, and
root sprung trees can also be found scattered
around the outside of the severely damaged
areas. The damage in the project area was
salvaged in 2005, to reduce fuel loading and
left to regenerate naturally. In Compartments
113 and 114 the tornado damage areas totaled
219 acres.
Riparian Vegetation (MA-4)
Species Composition – Riparian vegetation
varies along Lancaster, Forsythe, and Crib
Creeks, as well as several intermittent and
ephemeral tributaries. Hardwood tree species
dominate in some areas, while pines prevail in
other places. Some intermittent streams
reside in pine-dominated uplands, for
example.
The November 2004 tornado also damaged
pines and hardwoods in MA-4, along the
upper reaches of Lancaster and Forsythe
Creeks, as well as several intermittent and
ephemeral streams.
Structure – These areas are similar to the
upland forests in Lancaster-Forsythe Project:
even-aged with three layers. In some places,
a young hardwood forest has grown in place
of the mature pines killed by SPB.
Snags and coarse woody debris are present in
all stands, although the majority of this type
of material resides more in older stands.
Under the proposed actions, no logging would
take place within MA-4, but prescribed fire
would be allowed to back in, extinguishing
naturally.
ECS
According to the Ecological Classification
System (ECS) for the National Forests of the
West Gulf Coastal Plain, the Lancaster-
Forsythe Project, Phase I lies within the
Clayey Uplands Landtype Association.
Several Landtype Phases occur in this
Landtype Association and the project area:
1. Longleaf Pine-(Shortleaf Pine)-Blackjack
Oak/Schizachyrium Sandy Arenic Dry
Uplands
2. Shortleaf Pine-(Longleaf Pine)-Post
Oak/Callicarpa-Chasmanthium Loamy
Dry-Mesic Uplands
3. Shortleaf Pine-Post Oak/Chasmanthium
Clayey Dry-Mesic Uplands
4. White Oak-Loblolly Pine/Callicarpa
Loamy Mesic Lower Slopes and Terraces
5. White Oak-Water Oak/Mitchella-
Arisaema Loamy Mesic Stream Bottoms
6. Willow Oak-Laurel Oak/Bignonia Loamy
Wet-Mesic Stream Bottoms (Turner 1999,
p. 22-9 to 22-17).
These Landtype Phases have an overstory that
is highly variable, but usually consist of
mixed pine and hardwood species. In the
pine-dominated stands, the desired future
condition is to maintain the open understory,
provide habitat for RCW recovery, and
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Chapter 3. Alternatives, Including the Proposed Action Page 14 of 52
maintain an overstory dominated by large
pine trees with hardwoods scattered
throughout.
Old-Growth
No virgin stands occur in the Lancaster-
Forsythe Project, Phase I. Stands proposed
for treatment currently exhibit no unique old-
growth characteristics, other than natural
succession associated with second-growth
forests as they mature. Stands designated to
provide old- growth values would need to
experience the aging, natural processes, and
management techniques necessary to develop
old growth characteristics. While age is not
the sole criterion used to designate old-
growth, older stands are priority candidates
for consideration since they may provide old-
growth character sooner than younger stands.
Within the Lancaster-Forsythe Project, Phase
I, The Plan designates MA-4 (Streamside
Management Zones) as potential old-growth.
While older forest conditions will develop in
numerous areas throughout MA-2, no
allocations for old-growth are to be provided
(The Plan, p. 103).
Even though no allocations are to be provided
in MA-2, The Plan requires an evaluation of
all stands that are 95 years or older (The Plan,
Appendix I). Several stands are 115 years old
with a list of these stands in Table 3-5 below.
Table 3-5. Oldest Stands in Compartment 113 and
114.
Compartment
Stand
Age Forest
Type
113 2 115 31
10 100 31
15 115 31
16 115 31
22 115 31
23 115 31
24 115 31
26 115 31
28 115 31
114 2 101 31
3 100 31
7 115 31
10 115 31
14 115 31
17 103 31
18 110 31
22 115 31
24 115 31
27 115 31
28 115 31
30 115 31
35 115 31
37 115 31
38 115 31
39 115 31
40 115 31
42 110 31
43 85 31
31 - loblolly
According to The Plan, Appendix I, shortleaf
pine is the only forest type in which old-
growth designations are to be considered.
However, no shortleaf pine stand within the
Lancaster-Forsythe Project, Phase I
boundaries showed the characteristics
necessary to be designated as old growth.
Within Compartment 113 and 114, The Plan
designates MA-4 (Streamside Management
Zones) as potential old growth.
Fuels
As mentioned above, loblolly pine dominates
most of Compartments 113 and114,
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Chapter 3. Alternatives, Including the Proposed Action Page 15 of 52
interspersed with varying amounts of
shortleaf pine. Some areas in the two
compartments have a significant understory
shrub and hardwood component.
The dense shrub component contributes to
fire behavior in a number of ways. Fire
intensity, flame length, and rate of spread can
be increased when dense understory
vegetation provides “fuel ladders,” in which
dead pine needles and leaf litter can carry
flames into the tops of the understory
vegetation or into the crowns of the overstory.
Dense understories also limit visibility and
impede access of firefighters and equipment.
The prescribe fire frequency for each of the
two compartments is different. The east side
of Crib Creek was burned in 2006 (814 acres)
and the west side was not. In 2008 the whole
compartment (1,707 acres) was prescribed
burned. Compartment 114 has been burned
on a two-year cycle for the last ten years.
The current fuel loadings vary according to
the burn frequency – the longer the burn
rotation, the greater the fuel accumulation.
Most researchers agree that loblolly pine sites
probably burned at fire return intervals of 3 to
10 years and that fire intervals for shortleaf
pine typically ranged from 2 to 6 years (Wade
et al. 2000).
Condition Class is based on average number
of years between fires (fire frequency)
combined with the severity of the fire on the
dominant overstory vegetation. Condition
Class is a measure of the amount of departure
from the natural fire regime. The desired
condition, Condition Class 1, is considered a
moderate departure from natural conditions
where vegetation characteristics, fuel
composition, and fire behavior is within the
historical range of variability and there is a
low risk to key ecosystem components
(Schmidt et. al. 2002).
The USDA Forest Service developed fuel
models that rate fire danger and predict fire
behavior. Fuel load and depth are significant
fuel properties for predicting ignition, rate of
spread, and intensity (Anderson 1982).
According to the district fire staff, fuels
conditions in Compartment 113 and 114 most
closely resemble Fuel Model 2 and Fuel
Model 7. The west side of Compartment 113
(Cribb Creek), is best represented by Fuel
Model 7 due to the reduced frequency of
prescribe burning. In Fuel Model 7
characterized as Southern Rough, fires burn
through the surface and shrub strata with
equal ease and can occur at higher dead fuel
moisture contents due to the flammability of
live foliage (Anderson 1982). The east side
of Compartment 113 (Crib Creek) and all of
Compartment 114, are characteristic of Fuel
Model 2, due to the increased frequency of
prescribe burning. Fuel Model 2,
characterized as Timber, fires spread
primarily through the fine herbaceous fuels,
either curing or dead. These are surface fires
where the herbaceous material, besides litter
and dead-down stemwood from the open
shrub or timber overstory, contribute to the
fire intensity (Anderson 1982).
Characteristics of Fuel Model 2 and 7 are
shown in Tables 3-6 and 3-7 below.
Table 3-6. Fuel Model 2 Characteristics
Fuel Loading (tons/ac)
1 hour 2.0
10 hour 1.0
100 hour 0.5
Live woody 0.5
Live herbs 0.5
Fuel bed depth (feet) 1.0
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Chapter 3. Alternatives, Including the Proposed Action Page 16 of 52
Table 3-7. Fuel Model 7 Characteristics
Fuel Loading (tons/ac)
1 hour 1.1
10 hour 1.9
100 hour 1.5
Live woody 0.4
Live herbs 0.5
Fuel bed depth (feet) 2.5
Cumulative Effects Area
The Lancaster-Forsythe Project, Phase I is
located in the southeastern corner of the Davy
Crockett NF, which houses a sub-population
of RCW, and is the area to be considered for
cumulative effects to vegetation. This part of
the Davy Crockett NF stretches west from the
FM 2262 to FM 357.
Table 3-8 shows the various forest types
found in the Cumulative Effects Area.
Table 3-8. Forest types in Compartments 113 and 114
Forest Type Age Acres
Loblolly Pine 1-10 230
21-30 447
31-40 371
41-50 107
51-60 122
61-70 397
71-80 192
81-90 489
91-100 165
101-110 155
111-120 738
Shortleaf Pine 21-30 42
71-80 156
Southern Red Oak-Pine 21-30 110
Total 3,721
Private Land
Private land within the cumulative effects
area will not be considered for cumulative
effects to vegetation, because vegetation
management effects are independent of each
other. What occurs on other ownership has
no measurable effect on the national forest’s
vegetation.
3.6.2 Environmental Consequences
3.6.2.1 Alternative 1 (No Action)
Upland Forests (MA-2)
Species Composition - This alternative will
allow vegetation to continue to grow. Species
composition will change due to natural
occurrences such as insect and disease
outbreaks, wildfires, floods, and windstorms.
Tree mortality would increase as older stands
mature and become predisposed to insects and
disease.
Increasing rates of tree mortality can be
expected as loblolly pine stands exceed 80
years of age. Southern pine beetle hazard and
the potential for loss of large areas to SPB
infestation would increase as time passes for
much of the forest communities in the
Lancaster-Forsythe Project. If SPB did infest
this area, species composition could shift to
more tolerant hardwood species as pine trees
die. Hardwoods are already present in all
layers of the forest. These hardwoods have a
competitive advantage over pine regeneration
because their root systems are already well
established.
The young pine forest communities in the
Lancaster-Forsythe Project, Phase I would
also decline under this alternative. These
younger stands are more disposed towards
insect infestation than disease. Growth would
slow, which increases susceptibility to SPB.
As SPB hazard increases, the likelihood of
mortality would increase.
Without prescribed burning changes to the
midstory and understory vegetation would
occur. As time passes and fire is kept out of
the project area, the fire intolerant species,
such as magnolia, sweetgum, elm, holly,
mulberry, and cherry will increase in diameter
and height; the fire dependent species, like
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Chapter 3. Alternatives, Including the Proposed Action Page 17 of 52
shortleaf pine, will decrease in quantity and
may cease to exist. This has already
happened in the west Gulf Coastal Plain. Fire
suppression and land clearing have greatly
reduced the distribution of shortleaf pine
(Williams 1997).
Upland Forests (MA-2)
Structure - Structure of the forest
communities in the area will change more
slowly over time than species composition.
The potential does exist for some midstory
and understory hardwoods to grow into the
overstory, especially if SPB or other natural
disturbances eliminate portions of the canopy.
Snags and coarse woody debris would
increase in most areas, as the forest continues
to age.
Riparian Forests (MA-4)
The No Action Alternative would have little
effect on species composition and structure of
riparian areas.
ECS
This alternative would allow vegetation to
continue to grow. Natural succession and
occurrences would slowly alter the species
composition of the forest.
SPB could kill pine trees in both mature and
younger stands, and hardwoods could quickly
dominate. Lack of fire will help to increase
fire intolerant species and fire dependent
species such as shortleaf pine could cease to
exist. Long-term changes, such as species
extirpation would not be considered
consistent with ECS.
Old-growth
Older forest conditions will develop in
numerous areas throughout MA-2, but no
allocations for old-growth are to be provided
(The Plan, p. 103).
Fuels
The proposed prescribed burning will not be
conducted under this alternative. Fuel loads
in all stands will continue to increase in the
future. Increasing dead fuels, ladder fuels and
closer canopies increase the potential for
overstory mortality. Fuel loads will continue
to move toward high intensity, stand
replacement type fire regime. Condition
Class 2 (moderate risk of losing key
ecosystem characteristics due to wildland fire)
will be replaced by Condition Class 3 (high
risk of losing key ecosystem characteristics
due to wildland fire). The potential for a fire
to move off the forest and into the urban
interface (or vice versa) will increase as the
rate of spread of the fire increases. As a fire
burns with greater intensity it has larger flame
lengths and becomes more difficult to
suppress and resistance to control increases.
Private land, residences, and improvements
will continue to develope adjacent to federal
lands which have high fuel loads. Firefighter
safety will continue to be jeopardized by
intense fires with fast rates of spread.
Cumulative Effects
Vegetation management activities have taken
place in the cumulative effects area.
Prescribed burning, timber cutting, and insect
control have occurred at regular intervals. As
a result, the Cumulative Effects Area contains
a mosaic of young and old forest
communities.
Lack of thinning and prescribed burning
would result in a declining, over-mature forest
in Compartment 113 and 114, predisposed to
accelerated losses to insects, disease, and
wildfire. The understory would continue to
grow, and would become impenetrable,
particularly where the overstory has ceased to
exist. Young forest communities in the
Lancaster-Forsythe Project would continue to
grow and mortality would continue to
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Chapter 3. Alternatives, Including the Proposed Action Page 18 of 52
increase. Insect and disease would likely
destroy these stands.
From a fuels standpoint, the overall fuel load
in the project area will not be reduced and
resources in the area will continue to be at
risk for intense, difficult to control fires. Fuel
Model 7, with the potential for extreme fire
behavior, will continue to dominate the
project area. The No Action Alternative will
have no cumulative effects on vegetation in
MA-4.
3.6.3.1 Alternative 2 (Proposed Action)
Upland Forests (MA-2)
Species Composition –By favoring shortleaf
or loblolly in the thinning process, over time
we could change some specie composition in
the overstory. It will provide several benefits
including increased residual tree growth;
improved vigor of residual trees; improved
stand quality, as damaged and poorly formed
trees are removed; increased diversity within
stands; and improved ability of the stands to
withstand stresses such as drought and insects
(Smith, et. al. 1997, p. 87). Tree vigor is the
single most important factor to good tree
health. Tree and stand vigor provide the best
resistance to bark beetles in southeastern
North America (Nyland 1996, p. 456).
Indirect effects from the activities proposed
would be beneficial to the RCW. Although
past prescribed fire has reduced the woody
understory in many of the treatment areas,
there is a significant midstory problem
throughout the two compartments. In
addition, pine basal areas are quite high in
many stands. These two factors contribute to
habitat quality for the RCW being reduced.
The proposed thinning would target both
pines and hardwoods. Pine basal areas in the
mature stands to be thinned range from 73 to
122 sq. ft. per acre. These stands would be
thinned to an average BA of 70 sq. ft. per
acre. Approximately 2351 acres of mature
stands are proposed for thinning. This
thinning will create more open stand
conditions and increase spacing between
trees.
Some stands with relatively high basal areas
are not proposed for thinning because these
high basal areas are due to the large diameter
of the trees. It is felt that the spacing of the
individual trees is adequate, and if thinned,
the stand could quickly become too sparse if
even a few additional trees were lost to
lightning, windthrow, or other causes.
Thinning would also target merchantable
hardwoods. Site-appropriate hardwoods
would be retained, with up to 3-10 trees (> 5”
dbh) per acre being identified for retention.
Naturally occurring hardwood inclusions
would also be retained. Remaining
hardwoods would be commercially removed.
Coupled with the pine thinning, this would
help to create the open stand conditions
favored by the RCW.
Thinning would decrease the density of the
dominant cover and result in the development
of herbaceous plants, such as grasses, bracken
fern, and partridge pea. It will also stimulate
new woody growth in the understory.
Thinning will remove many of the smaller
and poorly formed stems from the stands,
which will allow the residual trees to attain a
larger average size and above average quality.
The SPB hazard will be reduced in the
thinned areas in the long term; however,
during the first year after thinning, the
disturbance of thinning may increase the risk
of pine beetle attack.
Currently, about 2,212 acres of the pine-
dominated forest communities, which is 59%
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Chapter 3. Alternatives, Including the Proposed Action Page 19 of 52
of all the acres in Compartment 113 and 114
(3,721 acres), have basal areas greater than
101 square feet per acre, which is considered
high hazard for SPB susceptiblity (Hicks, et.
al. 1980). Several of the pine stands in in
these two compartments fall within the
moderate and high SPB hazard rating. Left
alone, these stands will quickly grow into the
higher risk category.
Thinning could affect species composition in
the overstory by favoring select species to be
left and will have minimal effects on species
composition in the midstory and understory.
Thinning will encourage development of
herbaceous plants and also stimulative new
woody growth.
Prescribed burning will not really change the
species composition of the overstory.
Prescribed burning would help to reduce or
eliminate young hardwood trees and other
shrubby plant species, which would in turn
encourage herbaceous growth, grasses, and
forbs, in the understory (USDA 1989, p. IV-
38).
Historically, fire has always been part of the
ecosystems in the Gulf Coastal Plain. Tree
ring chronology from 1755-1995, using
stumps of loblolly and shortleaf pines blown
over in the February, 1998 windstorm on the
National Forests in Texas, showed a fire
frequency of 1.5 years. Dendrochronological
analysis shows long-term establishment of
fire dependent ecosystems in Texas (Jurney,
et. al. 2000).
Prescribed fire would be used to help achieve
the open upland pine-dominated forests
described as the DFC for Compartments 113
and 114. Relatively frequent fires, during
both the dormant and growing seasons, would
be used to restore fire dependent ecosystems.
Prescribed burning would temporarily reduce
the number of young hardwood trees and
other shrubby plant species within the
understory and midstory. The burning would
partially reduce the structural diversity of the
understory by the reduction or elimination of
some smaller midstory and understory
hardwoods and shrubs. Burning would
encourage herbaceous growth, grasses, and
forbs in the understory, at the expense of
woody growth (USDA 1989).
Prescribed burning is considered a natural
distrubance for the upland landtype phases. It
was an important environmental factor in
determining the structure and distribution of
upland communities on the pre-settlement
landscape (Van Kley et. al. 2007). Similarly,
prescribed burning planned in Alternative 2
will result in a mosaic of understory
conditions, since not all areas will burn and
some will burn with different intensity. Fire
will back into riparian areas and extinguish
naturally. This mosaic effect is not
inconsistent with ECS, which describes
variable intervals for landtype phases (Van
Kley et. al. 2007). In addition, The Plan
guides prescribed burning on a 3-7 year
rotation to manage various components of the
ecosystems (p. 91).
White oak, post oak, and hickories are all well
adapted to periodic fire: they all sprout from
the stump or root collar. Many of the
hardwoods found in the midstory and
understory of the upland forests, such as red
maple, dogwood, ash, blackgum, and
blackjack oak, are well adapted to fire. Trees
may be top-killed by fire, but all have the
ability to sprout from the stump or roots
(FEIS 2000).
Some hardwoods in the transitional zones and
on lower slopes of the uplands are less
resistant, or more susceptible to fire.
Magnolia is fire intolerant, partially because
of its thin bark. Still the species does possess
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Chapter 3. Alternatives, Including the Proposed Action Page 20 of 52
the ability to sprout from the stump. Elm is
easily damaged by fire but can sprout.
Sweetgum is highly susceptible to top-kill,
but also has the sprouting ability. Holly,
yaupon, cherry, eastern hophornbeam – all are
susceptible to fire and can be top-killed. All
possess the ability to sprout (FEIS 2000).
Upland Forests (MA-2)
Structure - Thinning would decrease the
density of the dominant cover and result in
the development of herbaceous plants, such as
grasses, bracken fern, and partridge pea. It
will also stimulate new woody growth in the
understory.
Some residual trees, both pine and
hardwoods, could receive some damage from
tree removal operations. Skidders can crush
or wound some ground vegetation and
understory species. Protecting mast
producing hardwoods in the overstory of pine
stands during thinning operations will ensure
retention and development of this component
in the pine stands. No more than 30 square
feet per acre of basal area will be removed
from the dominant or co-dominant trees. An
exception would be in pine plantations being
thinned for the first time where more than 30
square feet of basal area may need to be
removed to facilitate equipment used during
thinning operations.
Biologists studying forest types from nearly
every region of the country have made
consistent recommendations of retaining 2-4
snags per acre. While equipment used in
thinning has the potential to knock over snags
and break up existing coarse woody debris,
snags and recognizable den trees will be
retained and protected (The Plan, p. 55).
Controlling removal of dead, dying, and
decayed trees, emphasizing tree species that
are most likely to be recruited into the snag
population, and thinning stands to create
habitat conditions favorable to cavity-
dependent birds are some of the management
actions proposed to maintain adequate
densities of snags in southern forests (Lanham
and Guynn 1993). These suggested activities
are consistent with the proposed action.
Prescribed burning would partially reduce
structural diversity of the understory by
eliminating some vegetation in the lower
layers. At the same time, it will result in a
mosaic of understory conditions, since not all
areas will burn and some will burn with
different intensity. It will encourage
herbaceous growth at the expense of woody
growth (USDA 1989, p. IV-39). The
potential for scorching in the midstory and
overstory does exist. Light amounts of scorch
may increase growth and moderate crown
scorch does not affect the growth of
unthinned loblolly pine trees in the dominant
or co-dominant crown classes (USDA 1989,
p. IV-37).
Prescribed burning affects snags and coarse
woody debris in two ways - simultaneously
killing live trees and consuming dead trees.
Prescribed burning’s effect on snags and
coarse woody debris will also depend on
conditions such as fuel moisture, weather, and
firing techniques (Van Lear 1993).
Prescribed burning only occurs under certain
fuel and weather conditions to minimize risk
of resource damage. Within these self-
imposed parameters, consumption or
scorching of fallen logs should be minimal,
although degrees of consumption scorch will
vary according to topographic position. In
other words, snags and coarse woody debris
in the uplands would be more likely to be
partially consumed than those located closer
to streams.
Streamside Management Zones (MA-4)
Species Composition –The primary zone will
be a 50-foot protection zone to ensure primary
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Chapter 3. Alternatives, Including the Proposed Action Page 21 of 52
objectives of the area are achieved. This
primary zone will extend from the stream
channel edge outward 50 feet on either side of
the stream (The Plan, p. 152). Design criteria
developed by the Forest fisheries biologist
would help to protect stream banks and
existing vegetation.
prescribed fire would be allowed to enter
from adjacent uplands, extinguishing
naturally as conditions become moister.
Some hardwoods in these areas, such as
magnolia, elm, sweetgum, holly, yaupon,
cherry, and eastern hophornbeam are
susceptible to fire and can be top-killed. All
possess the ability to sprout (FEIS 2000).
Hardwood composition would change very
little, if at all.
Streamside Management Zones (MA4)
Structure - A transition zone will develop in
these areas as fire backs through and due to
the site’s moister conditions, goes out. Where
fuels exist in streamside zones to carry the
fire, some vegetation would be top-killed, but
as fire moves downslope or into moister
areas, fire intensity would decrease and less
of the existing vegetation would be affected.
Generally, pine needles would provide fuel
that would carry the fire better than hardwood
leaves; where pine exists in these moister,
lower slopes, the potential exists for fire to
top-kill shrubs and small hardwoods.
The effects on snags and coarse woody debris
from prescribed burning would be minimal in
these moister areas. Snags are more common
in hardwood stands and in lowlands and
riparian zones (Van Lear 1993). In fact, it is
the wet conditions associated with riparian
areas and the high moisture content of rotting
material that helps extinguish the fire as it
backs into these zones. Some snags and
fallen logs could be scorched, depending on
moisture conditions.
ECS Thinning would not affect species in the
overstory, and would have minimal effects on
species composition in the midstory and
understory. Thinning will alter structure
somewhat, encouraging development of
herbaceous plants and also stimulating new
woody growth. None of these effects are
inconsistent with the ECS.
Prescribed burning is considered a natural
disturbance for the upland landtype phases. It
was an important environmental factor in
determining the structure and distribution of
upland communities on the pre-settlement
landscape (Turner 1999, p. 4-7). Similarly,
prescribed burning planned in the Proposed
Action will result in a mosaic of understory
conditions, since not all areas will burn and
some will burn with different intensity. Fire
will back into riparian areas and extinguish
naturally. This mosaic effect is not
inconsistent with ECS, which describes
variable intervals for landtype phases (Turner
1999, p. 4-8). In addition, The Plan directs
prescribed burning on a two to five year
rotation as the preferred method to control
midstory vegetation and enhance RCW
habitat in MA-2 (The Plan, p. 110).
Old-growth
Evaluations conducted in all stands 95 years
and older showed that none of these areas are
actually old enough to be considered old-
growth. In accordance with The Plan, older
forest conditions will develop in numerous
areas throughout MA-2, but no allocations for
old-growth are to be provided (p. 103).
Vegetation management activities, such as
commercial thinning and prescribed fire
maintain characteristics consistent with old-
growth (The Plan, Appendix I).
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Chapter 3. Alternatives, Including the Proposed Action Page 22 of 52
Cumulative Effects
Vegetation management activities have taken
place in the cumulative effects area.
Prescribed burning, timber cutting, and insect
control have occurred at regular intervals.
Within the two compartments in the
cumulative effects area, about 33 percent of
the pine forest communities are less than 36
years old, following natural disturbances such
as SPB infestations and windstorms, as well
as some planned regeneration.
As a result of the various natural disturbances
and planned forest management, the
cumulative effects area contains a mosaic of
young and old forest communities.
Vegetation management activities such as
thinning and prescribed burning help to keep
the forest communities healthy and growing
towards the older conditions preferred by
RCW.
One ongoing project within the cumulative
effects area that could result in additional
effects to vegetation is midstory reduction.
This midstory reduction would alter structure
as woody understory is reduced and parts of
the forest become more open. These actions,
along with prescribed burning, would also
help to create a mosaic of shifting conditions.
As a result, the vegetation in several areas in
the Cumulative Effects Area would approach
the Plan’s Desired Future Condition for MA-
2.
The thinning and prescribed burning proposed
in the Lancaster-Forsythe Project, Phase I
would result in the development of open
forest conditions in the uplands, as overstory
density (thinning) and the woody understory
vegetation (prescribed burning) are reduced.
In addition to these changes in stand structure,
the November, 2005 tornado altered age class
distributions by creating several hundred
acres of openings in the canopy which will
now revert back to early seral stage following
salvage operations.
Older stands would continue to make up the
majority of the forest communities in the
Lancaster-Forsythe Project, Phase I area. The
reduction in the number of acres of forest
older than 60 years would be more than offset
by younger stands aging and entering this age
class.
The actions proposed in the Lancaster-
Forsythe Project, Phase I are similar to those
that have taken place in the last several years
on the Davy Crockett National Forest. The
end result is an open forest that provides
quality habitat for the red-cockaded
woodpecker and moves the Davy Crockett NF
towards the desired future condition for MA-
2. Cumulatively, MA-4 would not be
affected.
Climate Change
Ongoing research suggests that climate is
already changing, and impacts include
increases in air temperature, sea level, and
frequency of extreme weather, such as
hurricanes and droughts. These conditions
could eventually result in a more stressed
forest environment, which could in turn lead
to reduced growth and productivity. Declines
in tree and stand vigor may make forests more
susceptible to large-scale pest attacks and
other disturbances (Anderson 2008).
The proposed thinning will help to improve
the forest’s resistance and resilience to
climate changes (Anderson 2008). According
to the Intergovernmental Panel on Climate
Change, forest management can be used to
mitigate climate change, by maintaining
stand-level carbon density through reduction
of forest degradation, planting, site
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Chapter 3. Alternatives, Including the Proposed Action Page 23 of 52
preparation, and other management practices
(Nabuurs et. al. 2007).
The proposed prescribe burning would help to
reduce fuel loadings (Ryan 2008). The
amount of carbon dioxide released by a low-
intensity fire is small and the store of carbon
on the forest floor is rapidly replaced as fine
fuels re-accumulate and low shrubs regrow
(Underwood et. al. 2008).
Cumulatively, improving forest health and
reducing fuel loadings are considered
sustainable forest management strategies that
provide long-term benefits that mitigate
climate change (Nabuurs et.al. 2007).
Conclusions
Thinning about 2,351 acres of pine-dominated
stands and prescribed burning on
approximately 3,721 acres every 2-5 years
would improve RCW habitat.
Effects to vegetation from thinning,
prescribed burning, and midstory control
would create a more open canopy with
increasing amounts of herbaceous and grassy
species in the understory. These actions
would enhance the desirable species
composition and structure of the overstory.
The proposed actions would help to move the
forest toward the desired future conditions
described for MA-2.
The No Action and the Proposed Action
Alternative will have no cumulative effects on
vegetation in MA-4.
3.7 Threatened and Endangered Species
Federally Listed Threatened & Endangered
Species
Birds
Red-cockaded woodpecker (Picoides borealis)
Birds - Affected Environment and
Environmental Consequences
3.7.1 Red-cockaded Woodpecker (Picoides
borealis)
3.7.1.1 Environmental Baseline
The red-cockaded woodpecker (RCW) has
high potential to occur on drier ridgetops in
open-canopy, fire-maintained, mature pine
stands with forb and/or grass dominated
ground cover and a midstory relatively devoid
of hardwoods (Hovis and Labisky 1985;
Jackson 1994; Conner et al. 2001; Walters et
al. 2002; USFWS 2003). The species has
moderate potential to occur in mature, pine-
dominated stands with a mixture of
hardwoods and hardwood midstory, as is
present throughout much of the Davy
Crockett National Forest. The RCW
excavates cavities in live pine trees, using
older trees infected with red heart fungus
(Phellinus pini), thin sapwood and a large
diameter of heartwood (Conner et al. 1994;
Conner et al. 2001). Generally, pines ≥60
years old are needed for cavity excavation
(Rudolph and Conner 1991; USFWS 2003).
Threats to this species include conversion of
mature forest to short-rotation plantations or
non-forested areas, hardwood proliferation
resulting from fire exclusion, lack of forest
management to develop and maintain open
stand conditions, and habitat fragmentation
that affects population demographics.
Most of the pine dominated stands in the two
compartments are composed of trees that are
of suitable age (≥60 yrs.) for cavity
excavation (Rudolph and Conner 1991, p.458-
467; USFWS 2003, p.34). However, these
stands have a high pine density and/or a well
developed hardwood midstory, and do not
provide high quality nesting or foraging
habitat for this species (USFWS 2003).
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Chapter 3. Alternatives, Including the Proposed Action Page 24 of 52
This species has a high potential to occupy
proposed treatment areas because it has been
documented in some of these areas.
The RCW population trend is presently
increasing slowly but steadily on the National
Forests in Texas (Fig.1; USFS 2007,
Appendix A, p. 23).
Fig. 3-1. National Forests in Texas-wide RCW
population trend 1988-2009 (USFS 2007, Appendix
A, p. 23 and J. Nolde).
The RCW population on the DCNF is
composed of the northern and the Alabama
Creek subpopulations. This project is located
within the Alabama Creek subpopulation.
Following a period of relative stability, the
DCNF population began to grow in 1998
(Fig. 2). However, this growth stalled in
2001, after a restraining order restricted
prescribed burning for several years,
beginning in 1999, mostly to areas having
existing NEPA decisions. However, with the
lifting of the restraining order in 2003, the
population began to rebound in 2004 in
response to increased burning in RCW areas.
Fig. 3-2. RCW population trends 1991-2009 on the
Davy Crockett National Forest, # groups by
subpopulation (data from various DCNF biologists
and USFWS biologist J. Reid).
The DCNF is identified as a secondary core
population, with a population objective of 250
potential breeding groups (USFWS 2003).
The Forest presently (spring 2009) supports
72 groups. This figure includes 70 potential
breeding groups and two single bird groups
(one each in the northern and Alabama Creek
subpopulations)
Available Inventories
Systematic ground surveys (transects) for this
species were conducted in c-113 and 114 by
Forest Service personnel experienced in
identifying RCW cavity trees in February and
March 2010. No undocumented cavity trees
were found. Pine-dominated stands > 60
years old (high potential habitat and future
high potential habitat) were surveyed.
Additionally, district personnel survey a
sample of clusters and recruitment stands
annually for status (active/inactive) and
document new cavity trees (including starts)
at that time.
Morning roost checks were completed to
determine group size and to identify currently
active trees. Table 3-9 displays the results of
those morning roost checks. Group sizes may
be artificially inflated in some instances due
to the presence of an occasional juvenile bird
0
50
100
150
200
250
300
350
1988 1992 1996 2000 2004 2008
Active Clusters
0
10
20
30
40
50
60
70
80
All DCNF*
Al. Crk.
DC north
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Chapter 3. Alternatives, Including the Proposed Action Page 25 of 52
that may not yet have dispersed, but most are
probably accurate.
Table 3-9. Group size of RCW groups in
Compartment 113 and 114.
Cluster # Birds Cluster # Birds
113-1 5 114-1 5
113-2 6 114-2 6
113-22 2 114-28 3
113-23 0 114-33 5
113-25 3 114-37 2
114-43 3
Compartment 113 contains four active
clusters and one inactive cluster.
Compartment 114 contains six active clusters
and three recruitment clusters. One of those
recruitment clusters, stand 31, is proposed for
deletion due to its poor location along a
riparian area.
At a population density of one group per 200
acres of pine-dominate forest type,
Compartments 113 and 114 have a population
objective of approximately 18 groups. With a
current population of 10 groups, eight
recruitment clusters are needed. Three
suitable ones (the inactive cluster in c-113 and
the two RCs to be retained in c-114) are
already identified, leaving a need for five
additional recruitment clusters. Considerable
room remains in the western portion of c-113
for establishment of several of those
recruitment clusters.
Available inventory information is adequate
because inventories of high and moderate
potential habitat within proposed treatment
areas are current enough to guide project
design, support determination of effects, and
meet requirements for conservation of this
species.
This project is within Management Area
(MA)-2, Red-Cockaded Woodpecker
Emphasis. A goal of MA-2 is to “provide the
best possible habitat for the recovery of RCW
populations and sub-populations” (the Plan,
p.102). Management in MA-2 is directed
toward developing future conditions
consisting of “open pine forests mixed with
some hardwoods species” (the Plan, p.98).
This includes a frequent fire regime that
would create an “open, grass-like
understory.”
Most of the analysis area occurs in stands
with a pine-dominated forest type. Of these
pine dominated stands, most acres are
composed of trees that are suitable age (≥60
yrs.) for cavity excavation (Rudolph and
Conner 1991; USFWS 2003). However,
these stands generally have a high pine
density and/or well developed hardwood
midstory, and do not currently represent high
potential habitat for the RCW. There are
several large pine plantations in the
compartments that are as yet too young to
provide good RCW habitat, and are densely
stocked.
Habitat in the analysis area does not presently
meet the desired condition of MA-2, and also does
not meet the definition of good quality foraging
habitat (the Plan, p.98; USFWS 2003). Good
quality foraging habitat is defined in the Red-
cockaded Recovery Plan as habitat that has some
large old pines, low densities of small and
medium pines, sparse or no hardwood midstory,
and a groundcover of bunchgrass and forbs
(USFWS 2003). Habitat in the analysis area
contains an understory of yaupon, wax myrtle,
and other woody shrubs that ranges from
relatively light in some areas, to moderate or
dense in others. There is also a moderate to dense
midstory of small and medium diameter hardwood
trees, and the pine basal area is higher than
desirable.
A foraging habitat analysis was completed for
clusters in compartments 113 and 114, as well as
those in neighboring compartment 115 and 116
whose half-mile foraging circles extended into
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Chapter 3. Alternatives, Including the Proposed Action Page 26 of 52
one of the two analysis compartments. The
procedure used involved establishing a centroid
for each cluster and drawing a one half-mile
diameter circle around each. All pine stands 60
years and older within that circle, that were
contiguous and not separated for more than 200
feet, were counted for that cluster. Where circles
overlapped, a GIS program was used to apportion
acres.
Acreage for riparian areas, food plots, roads, and
other openings was not included in foraging
calculations. A 100 foot wide buffer (50 feet on
either side of the stream) was removed from
calculations, as this is the width of the primary
zone for most streams, and is the area where
management generally does not occur. Foraging
acreage was calculated by GIS specialist J.
Guedry. Foraging was calculated first using only
pine stands 60 years and older, and again
including stands 30-59 years of age. Table 3-10
contains the acreage of foraging habitat allotted to
each cluster by the two analyses. Table 3-10. Acres of foraging habitat (pine
stands > 60 yrs. Old and those 30-59 yrs. old +
those > 60 yrs. old) available to each RCW
cluster. Each cluster needs a minimum of 120
acres.
Cluster Status
Acres* (stands 60+ yrs only)
Acres* (includes stds 30-59
yrs)
Acres* 30+ yr stds,
excluding non-
thinned stds.#
113-1 ACTIVE 84.5 125.0 102.0
113-2 ACTIVE 87.2 158.1 103.1
113-22 Inactive 116.2 172.2 138.6
113-23 ACTIVE 126.1 198.7 68.2
113-25 ACTIVE 163.7 251.1 182.2
114-1 ACTIVE 142.3 179.3 80.0
114-2 ACTIVE 130.9 147.3 50.8
114-28 ACTIVE 168.7 191.1 176.2
114-33 ACTIVE 80.0 127.6 127.6
114-37 ACTIVE 161.0 161.0 149.8
114-42 Rc 177.1 177.1 177.1
114-43 ACTIVE 198.1 202.2 202.2
114-44 Rc 107.2 141.3 123.5
Cluster Status
Acres* (stands 60+ yrs only)
Acres* (includes stds 30-59
yrs)
Acres* 30+ yr stds,
excluding non-
thinned stds.#
116-1 ACTIVE 183.3 197.1 197.1
116-33 ACTIVE 147.6 163.1 159.9
116-34 ACTIVE 111.7 111.7 111.7
*Acreages in bold indicate limited foraging
# These figures do not include stands with higher BAs
that were not thinned, but that have appropriate spacing
between trees and thus provide good quality habitat.
As can be seen from the table, five RCW stands
(three active clusters and two inactive/recruitment
clusters) in the treatment area are limited in the
number of acres of mature (60+ year old pine
forest) available to them within ½ mile. An
additional three clusters (two active, one inactive)
within ½ mile of the treatment area (whose
foraging circles encompass part of compartment
114) also have limited foraging acreage. A map
(attached) shows the distribution of limited and
unlimited foraging acres in compartments 113 and
114.
The cumulative effects analysis area for this
species consists of compartments 113/114, the
remaining compartments in the southern
(Alabama Creek) Habitat Management Area (112,
115-121), and private lands surrounding these
national forest lands.
3.7.1.2.1 Alternative 1 (no action)
Direct and Indirect Effects
Because no management actions would occur
under this alternative, no direct effects would
occur to the RCW. Indirect effects would be
detrimental. Habitat quality in the analysis
area would decline or remain unsuitable for
this species. Densely stocked stands with
closed canopies would restrict sunlight to the
forest floor, thus inhibiting the establishment
of a grassy understory. Similarly, in lower
density stands, the lack of prescribed fire
would permit the continued development of
the woody understory and midstory. This
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Chapter 3. Alternatives, Including the Proposed Action Page 27 of 52
would serve to reduce open conditions and
suppress the desired understory vegetation.
These conditions would render any existing
high potential habitat unsuitable for
occupation, and ultimately impede potential
habitat from attaining the appropriate open
stand structure required by the RCW.
Cumulative Effects
Past prescribed burning has kept the woody
understory species somewhat controlled in
some areas of these two compartments. Over
time it is likely that habitat quality would
decline, resulting in an eventual decline in the
number of RCW groups in compartments 113
and 114. Nearby private lands provide little
habitat for the RCW. Much of the lands
surrounding these two compartments are in
pastureland, which cannot sustain this species.
The small amount of forested habitat that is
present is of only marginal quality due to
heavy hardwood midstory.
3.7.1.2.2 Alternative 2
Direct and Indirect Effects
This project would aid in the establishment or
improvement of upland pine habitat with the open
forest structure required by this species. Negative
direct effects from pine thinning and hardwood
reduction are not anticipated because no actions
would not take place within active clusters during
the nesting season or until nesting is completed
(the Plan, p. 115). Outside the nesting season no
work would occur in active clusters until one hour
after dawn, and would cease one hour before
sunset to avoid disturbing birds entering and
leaving roost trees.
Indirect effects from the activities proposed would
be beneficial to the RCW. Although past
prescribed fire has reduced the woody understory
in many of the treatment areas, there is a
significant midstory problem throughout the two
compartments. In addition, pine basal areas are
quite high in many stands. These two factors
contribute to habitat quality for the RCW being
reduced.
The proposed thinning would target both pines
and hardwoods. Pine basal areas in the mature
stands to be thinned range from 76 to 122 sq. ft.
per acre. These stands would be thinned to an
approximate BA of 70 sq. ft. per acre.
Approximately 1566 acres of mature stands are
proposed for thinning. This thinning will create
more open stand conditions and increase spacing
between trees.
Some stands with relatively high basal areas are
not proposed for thinning because these high basal
areas are due to the large diameter of the trees. It
is felt that the spacing of the individual trees is
adequate, and if thinned, the stand could quickly
become too sparse if even a few additional trees
were lost to lightning, windthrow, or other causes.
Thinning would also target merchantable
hardwoods. Site-appropriate hardwoods would be
retained, with up to 3-10 trees (> 5” dbh) per acre
being identifies for retention. Naturally occurring
hardwood inclusions would also be retained.
Remaining hardwoods would be commercially
removed. Coupled with the pine thinning, this
would help to create the open stand conditions
favored by the RCW.
Additionally, approximately 785 acres of younger
stands, 20-35 years old, will be thinned. Basal
areas are over 120 sq. ft. per acre in most of these
stands, although a few are lower. Thinning these
younger stands will increase the growth rates of
the remaining pines due to less crowding and
competition, and will reduce their vulnerability to
beetle infestation.
Following thinning, midstory reduction using
either mechanical equipment such as a rotary head
mulcher or other equipment, or handtools
(chainsaw, etc.) would be used in those stands that
still did not meet the definition of good quality
foraging habitat due to the presence of small
diameter hardwoods and/or the presence of
excessive woody understory that it was
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anticipated prescribed fire would not control
adequately.
An additional 871 acres that are not to be thinned
under this proposal would receive midstory
reduction treatment with handtools as needed to
help meet the qualities of good quality foraging
habitat. Some of these stands were thinned during
a previous small sale in c-113.
Hand tools would be used to release young pines
from competition on about 219 acres in three
stands. These are areas that were damaged by
tornadoes. The pine regeneration in these stands
is mostly or all loblolly pine.
All acreage in the two compartments (3721 acres)
would be prescribe burned every 2-5 years. This
would control resprouting of hardwoods and
woody understory species, helping to maintain the
open understories favored by the RCW. In
addition, frequent fire would stimulate
germination of grasses and forbs, encouraging
development of a diverse ground cover.
Given the past frequent use of fire in these two
compartments, the woody understory has been
greatly reduced in many areas, giving these areas
a head start on developing the diverse, herbaceous
ground cover found in healthy, restored pine
ecosystems. This is likely reflected in part by the
healthy RCW group sizes in the two
compartments. Average group size for the 4
groups in c-113 is 4.0 birds, and average group
size for the 6 groups in c-114 is also 4.0.
Group size is one of the strongest measures of
population health and stability, and group sizes
over 2.5 indicate that, on average, over half of the
groups have a helper. It is likely that the extra
large group sizes observed in these two
compartments partially indicate a healthy
population, but may also indicate a need for
recruitment stands to allow helpers to move out
and establish new breeding groups. Recruitment
stands will be established following completion of
habitat improvement work in these compartments.
As previously noted in Table 2, foraging habitat is
limited for some clusters without inclusion of 30-
59 year old pine-dominated stands. In their
current condition, most of the younger stands (30-
59 years) represent very low quality foraging
habitat. The first foraging map depicts foraging
habitat presently available to clusters in compts.
113 and 114, and to nearby clusters in adjacent
compartments 115/116, without including these
younger stands. Six stands lack the requisite 120
acres of foraging habitat.
With the inclusion of these younger stands, which
will be thinned and midstoried, in the foraging
analysis, five of the six stands no longer lack
limited foraging (Table 2) as shown on the second
foraging map.
As previously noted, a number of stands with
relatively high basal areas are not being thinned.
The high BAs in these stands are the result of
large diameter trees. Tree spacing meets the 20-
25 ft. minimum recommendation for RCW
habitat, and exceeds it in some of the stands.
Average pine diameters in some of these stands
are as high as 18.5” to 20.9” . Some of the stands
have as few as 38-53 trees per acre. For example,
std. 10 in C-114, with a BA of 92, has 38 pines
per acre, with an average BA of 20.9”. Stand 2 in
C-113, with a BA of 98, has 46 trees per ac., with
an average BA of 18.9”. Thus, even though these
stands have high pine basal areas, thinning them
to a BA of 70 would result in a sparse stand.
Table 2 shows foraging availability without
including the high-BA stands that are not
proposed for thinning. However, these stands will
still qualify as foraging habitat, since they will be
treated for midstory and burned, and they already
have the open, widely spaced nature needed by
the birds.
The habitat improvement work proposed for c-113
and 114 will improve the quality of existing
foraging habitat in the compartments, moving it
toward the ideal of good quality foraging habitat
as described in the revised RCW Recovery Plan
(USFWS 2003). The process of achieving that
ideal will be ongoing, with frequent use of
prescribed fire needed to control woody regrowth
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and foster the necessary grassy, herbaceous
ground cover.
Neither the RCW nor its habitat would be affected
by the proposed roadwork, including culvert
replacement and resurfacing.
Temporary road construction would involve
removal of some extra trees during right-of-way
clearing. However, the number removed would
be negligible in relation to the size of the analysis
area and is not expected to significantly affect
foraging availability. No roads would be built
through RCW clusters.
Control of nonnative invasive plant species would
not impact the RCW or high potential habitat for
the species. Control efforts would be directed at
individual plants and would not involve large-
scale clearing.
Cumulative Effects
In addition to the work proposed for c-113/114,
additional projects will be considered for other
compartments in the Alabama Cree
subpopulation. Adjacent compartments 112, 115
and 116 will be the next area to be evaluated for
habitat improvement needs. Work in those
compartments will benefit some of the clusters in
compartments 113 and 114, as their foraging
circles extend into one or both of those
compartments.
Nearby private lands provide little habitat for the
RCW, and the little pine habitat that is present is
of poor quality due to heavy hardwood midstory.
Most of the land surrounding these two
compartments is rural pastureland, wi
The cumulative effects analysis area for this
species consists of compartments 113/114, the
remaining compartments in Alabama Creek
WMA (112, 115-121), and private lands
surrounding these national forest lands.
3.8 Sensitive Species
Regional Forester’s Sensitive Species
Mammals
Rafinesque’s big-eared bat (Corynorhinus
rafinesquii)
Insects
Texas emerald dragonfly (Somatochlora
margarita)
Fish
Sabine shiner (Notropis sabinae)
Freshwater Mussels
Sandbank pocketbook (Lampsilis satura)
Louisiana pigtoe (Pleurobema riddellii)
Texas heelsplitter (Potamilus
amphichaenus)
Crayfish
Blackbelted Crayfish (Procambarus
nigrocinctus)
Neches Crayfish (Procambarus nechesae)
Sabine Fencing Crayfish (Faxonella
beyeri)
Mammals - Affected Environment and
Environmental Consequences
3.8.1 Rafinesque's Big-eared Bat (Corynorhinus rafinesquii)
3.8.1.1 Environmental Baseline
This bat reaches the western limit of its range
in eastern Texas. The Rafinesque’s big-eared
bat is primarily a solitary species that roosts
in hollow trees, crevices behind loose bark,
and under dry leaves (Davis and Schmidly
1994). It has also been observed roosting in
buildings, abandoned mines, and wells (BCI
2001; Menzel et al. 2003).
Research on habitat associations for this bat in
eastern Texas indicates that it has high
potential to occur within mature bottomland
hardwood communities containing large
diameter, hollow hardwoods, often of the
genus Nyssa, within one kilometer (0.6 mile)
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of water (Mirowsky and Horner 1997). This
research found that this bat preferred to roost
in these large, hollow hardwoods. Lance et
al. (2001) found big-eared bats roosting under
concrete bridges as well as in large hollow
Nyssa in Louisiana. Bridges used by these
bats were always associated with a higher
percentage of surrounding mature hardwood
forest than were unused bridges. A similar
affinity for hardwood-dominated roosts near
water was found for big-eared bats in South
Carolina (Bunch et al. 1998). Thus, two
important components of high potential
habitat across the range of the species are
mature bottomland hardwood forest and the
close proximity of water.
High potential foraging habitat for these bats
is bottomland hardwood forest. This bat is
considered a moth specialist (Hurst and Lacki
1997; Lacki and Ladeur 2002). The big-eared
bat usually forages by gleaning; that is,
picking insects off vegetation, and has been
observed to forage quite low, within 1 m of
the ground (Mirowsky and Horner 1997; BCI
2001).
This species of bat does not have high
potential to occupy proposed treatment areas
because these areas do not include high
potential habitat as described above.
However, the big-eared bat has been known
to occasionally forage in upland areas
adjacent to their preferred bottomland
foraging habitat, although such upland areas
represent only marginal habitat.
The big-eared bat displays a bimodal pattern
of foraging activity, common to a number of
bat species; that is, they forage for several
hours soon after dark, and again for a few
hours in the morning before returning to their
day roosts before dawn (Menzel et al. 2001).
Between foraging bouts, they likely rest in
temporary night roosts in or near their
foraging areas. Bats may use a variety of
sites for these temporary roosts, depending
upon what is available. The big-eared bat,
which occasionally forages in upland areas or
non-hardwood stands adjacent to high
potential bottomland foraging areas, may use
snags with loose bark or cavities, or upland
hardwoods with cavities, as temporary roost
sites.
This species is experiencing a population
decline across its range. The greatest threat
facing the big-eared bat is loss of bottomland
forest roost habitat (Bunch et al 1998;
Natureserve 2010), particularly the large
hollow trees needed for maternity roosts.
The cumulative effects analysis area for this
species consists of the two compartments
covered in this proposal, adjacent
compartments, and private lands surrounding
these national forest lands.
Available Inventories
No inventories were conducted for this
species specifically for this project, because
high potential habitat does not occur in the
treatment areas and the species does not have
high potential to occur in the treatment areas.
Any use of the treatment areas by this bat
species would be rare, and would occur only
occasionally during foraging. There are no
extensive, mature, low-lying floodplain
forests (high potential habitat) in the two
compartments covered under this proposal.
Thus, it was determined that no inventories
were needed.
3.8.1.2.1 Alternative 1 (no action)
Direct and Indirect Effects
Because no management actions would occur
under this alternative, no direct effects would
occur to this bat species.
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There would be little potential for indirect
effects to the big-eared bat. Densely stocked
pine stands are more susceptible to wildfire
and SPB infestation. These disturbance
events may create snags, particularly in
mature stands, that could serve as potential
temporary night roost sites. In addition,
failure to thin the stands to create open
conditions would likely leave them
unattractive to foraging bats, since such
stands would likely support few nectar
sources that might attract moths. Overall,
indirect effects would be those of natural
forest succession and aging, and could
potentially include the loss of larger acreages
to wildfire and/or beetle infestation.
Cumulative Effects
Bottomland habitat and hardwood stands on
national forest land would remain unchanged
as a result of this project, and continue to
contain high potential roost habitat.
However, this alternative would increase the
vulnerability of upland pine stands to wildfire
and SPB infestation. Although these
disturbances may create snags, they may also
result in the loss of mature stands. Because
the severity of these events is difficult to
predict, it is uncertain how long these stands
would persist to supply potential temporary
roosting habitat.
Adjacent private land uses generally do not
promote the preservation or development of
high potential roosting habitat. Hardwood
bottomlands contain the best quality habitat
for this species. However, the probability of
this habitat type persisting on private land is
low, as the overall trend has been a general
loss of bottomland hardwood forest. This
trend will likely continue on private land.
Human structures (abandoned buildings,
bridges, etc.) may also provide some roosting
habitat, but specific environmental conditions
must exist.
3.8.1.2.2 Alternative 2
Direct and Indirect Effects
Thinning and prescribed fire could potentially
displace or harm individuals. However, this
species has a preference for roosting in low-
lying hardwood communities, in which
thinning would not occur and prescribed fires
tend to burn at low intensity. Additionally,
high potential roost habitat does not occur in
c-55/56; thus it is relatively unlikely that the
species inhabits the compartment, although it
may occasionally forage in some areas. The
Rafinesque’s big-eared bat does not hibernate
in Texas (Davis and Schmidly 1994, p.66;
BCI 2001, p.48). This species would
therefore be mobile and alert during winter,
allowing for a high likelihood of escape from
an approaching fire or other disturbing
activity.
This is a slight potential for indirect effects.
Direct or inadvertent removal of snags may
occur during timber harvest or prescribed
burning. Both the number and distribution of
snags could be affected by the proposed
prescribed burning. Prescribed burning
would result in both the loss of existing snags
and the creation of new ones (Van Lear
1993). Prescribed fire has the potential to
reduce the number of snags in upland habitats
over time, although data collected by Dr.
Richard Conner at the Southern Forest
Experiment Station in Nacogdoches, Texas
has shown that large diameter snags will often
persist in upland areas even in the presence of
a prescribed burning program.
In addition, snags are more frequent in
lowlands and riparian areas than on upland
sites (McMinn and Hardt 1993; Van Lear
1993), including in the streamside
management zones throughout the
compartments, where fire would burn at lower
intensity. Based on this information, it
appears clear that there will continue to be
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adequate snags distributed across the
landscape to provide temporary night roosts
for foraging bats.
Thinning would reduce the potential for loss
of forested habitat to beetle infestation or
wildfire. Dense pine stands are more
vulnerable to beetle attack and wildfire
(Turchin et al. 1999; Boyle et al. 2004).
Thinning both the pines and hardwoods in
mature pine stands, followed by midstory
reduction where needed, would also create
more open stand conditions, favoring nectar
plants that would support moths, which are a
major food of this species. Thus, the
proposed work would be beneficial to any
bats using these compartments.
Thinning the younger pine stands would
shorten the time until they, too, provided such
habitat, as it would increase the growth rates
of the remaining pines due to the decrease in
crowding and competition. Prescribed
burning would help control woody understory
species and promote grasses and forbs,
including nectar-producing plants.
The proposed road work (resurfacing, culvert
replacement, etc.) would not impact bats, as it
would not alter bat habitat.
Construction of temporary roads would result
in the removal of some trees, but the number
removed would be negligible in light of the
number of trees present in the treatment areas.
Control of nonnative invasive plants would
not affect bats, since these species, such as
Chinese tallow, Japanese climbing fern, and
others, tend to not be nectar plants that might
attract moths and other bat prey species.
Removal of these invasives, as well as any
invasive plants that might attract bat prey
would benefit bats by reducing competition
with native nectar plants.
Cumulative Effects
Thinning and prescribed burning would
decrease the potential for pine loss from
wildfire and SPB infestation. This would
improve the likelihood of upland stands
retaining large pines that may become snags
or that have the structural characteristics for
roosting.
Surrounding compartments are managed
similarly to the compartments covered by this
proposal. High potential habitat is limited to
the larger river drainages, such as along the
Neches River. These areas are not in the
compartments included in this proposal.
Forest management on adjacent private land
provides little opportunity for the retention or
development of high potential roosting habitat
for this species. Most surrounding private
lands are in pasture or small woodlots. Lands
managed intensively for wood production
generally have lower densities of snags than
national forests (Van Lear 1993). Bottomland
forests and larger riparian forests have been
largely cut over on private lands, leaving few
large hollow trees that could provide high
potential roost habitat for this species.
Because forest management on private lands
is unlikely to change in the foreseeable future,
habitat in these areas would likely remain
limited.
Insects - Affected Environment and
Environmental Consequences
3.8.2 Texas Emerald Dragonfly (Somatochlora margarita)
3.8.2.1 Environmental Baseline
The Big Thicket emerald dragonfly has a
potential range that may exceed 10,000 square
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miles in southeastern Texas, including all four
national forests in Texas (Price et al. 1989).
This species was originally described from
the Sam Houston National Forest (Price et al.
1989). High potential habitat for larvae is
associated with small, clear, sandy-bottomed
streams and boggy seeps within loblolly and
longleaf pine stands (NatureServe 2010).
Adults are generalists, foraging for insects at
canopy level in mature forest and over gravel
roads and small openings. Because of its
specific needs, the larval stage of this species
is considered to be the critical life stage.
Threats to this species include clearing of
large areas of mature forest for conversion to
agricultural land or similar use, which would
displace adults; sedimentation of larval
habitat is a serious threat as well (Price et al.
1989; Natureserve 2010).
Larvae of this species do not have high
potential to occupy proposed treatment areas
because these areas do not include high
potential habitat (clear, sandy-bottomed
streams) as described above for larvae.
Although prescribed fire may burn into some
streamside zones, effects on vegetation would
be minimal. Fire will not affect streams
directly. However, because of the small
chance of indirect effects to larval habitat, this
species is included in the analysis.
Available Inventories
No systematic inventories for this species
have been conducted recently on the DCNF.
Price et al. (1989) surveyed two locations on
the DCNF, and found this species at both
locations. One location was in the northeast
portion of the forest, in/near compartments
17/18/19. The other was in the southern part
of the forest, in/near compartments 108/112.
Available inventory data are adequate.
Due to possible downstream impacts to water
quality, the cumulative effects analysis area
for this species includes streams in adjacent
compartments and private lands that flow into
the analysis areas, as well as downstream
areas in adjacent compartments and on private
lands.
3.8.2.2.1 Alternative 1 (no action)
Direct and Indirect Effects
Because no actions would occur under this
alternative, no direct effects would occur to
the Texas emerald dragonfly. However, this
alternative may increase the vulnerability of
pine stands to wildfire and SPB infestation.
While small openings created by beetle
infestations may be used by foraging adults,
the loss of large acreages of mature forest
could have negative effects on this species.
Wildfire, if intense, may remove riparian
vegetation, including the root mat, which
functions to impede soil movement.
Increased sediment delivery to streams,
particularly after heavy rain storms, would
impact water quality. However, the impact of
wildfire on riparian vegetation is difficult to
predict, and would greatly depend on fire
intensity. In the absence of larger wildfires,
this alternative would not affect dragonfly
larvae.
Cumulative Effects
Existing ongoing erosion problems from past
firelines would begin to heal on their own,
although sedimentation would continue on
some sites. Without replacement, some
culverts would continue delivering sediment
to streams, further degrading stream quality
(Peterson 2010).
Disturbances to streams from private land
uses would continue because current
management practices are not expected to
change. Adjacent private lands possess few
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areas of mature pine, and due to management
practices, are unlikely to provide high
potential habitat for the Texas emerald
dragonfly in the future. Most adjacent private
land has been cleared for pasture land, and
this trend is likely to continue.
3.8.2.2.2 Alternative 2
Direct and Indirect Effects
Given that the adult Texas emerald dragonfly
is highly mobile, negative direct effects from
thinning, midstory reduction, and prescribed
burning are unlikely to occur. Indirect effects
on adults are also not anticipated. Timber
harvest would not result in clearing of large
areas of mature pine, and therefore would not
negatively affect the suitability or availability
of foraging habitat for adults.
Although timber removal and midstory
reduction would not occur within the primary
zone of MA-4, associated actions have the
potential to cause sediment movement.
Temporary stream crossings, in particular,
may increase sediment delivery to streams.
However, long-term adverse impacts to
dragonfly larvae are not anticipated. Stream
crossings would be avoided and alternative
routes used to access harvest units when
possible. When in use, these crossings would
be used for a limited time, and would be
identified and designated in accordance with
the Forest Plan (USFS 1996, p.158).
The proposed thinning may result in
temporary increases in sediment delivery to
streams (Binkley and Brown 1993).
However, adverse effects to larval habitat are
not anticipated. Forest Plan measures and
project design criteria for protecting stream
courses would be followed (USFS 1996, p.82-
83, 153-154, and 158-159). These practices
limit sediment delivery to streams, and are
consistent with, or more restrictive than, state
Best Management Practices (BMPs) for
protecting aquatic habitats from
sedimentation. Prud’homme and Greis (2002,
p.524) found that the scientific literature and
monitoring results in the south demonstrate
that appropriate BMPs, fully implemented as
designed and adapted to a site, effectively
protect water chemistry, aquatic habitat, and
aquatic biota.
This alternative would involve burning and
the construction of fire lines within MA-4. A
major problem associated with prescribed fire
and water quality is potential increases in
sedimentation (Stanturf et al. 2002).
However, most studies in the south indicate
that effects of prescribed fire on water quality
are minor and of short duration when
compared with the effects of other forest
practices (Stanturf et al. 2002). Prescribed
fires in MA-4 tend to consist of low intensity
backing fires. Even intense burns may disturb
the root mat very little, leaving its soil-
holding properties intact (Stanturf et al.
2002).
Fire lines constructed near streams are to be
constructed by hand within the 50 foot-wide
primary zone, minimizing soil disturbance
and the extent of sediment movement. If this
direction is followed, there would be little
potential for indirect effects to aquatic habitat,
provided that these hand lines are constructed
so as to prevent or minimize sediment
delivery to streams. However, past fireline
construction on the DCNF has not followed
standards and guides in the Forest plan (USFS
1996) designed to protect streams and
soil/water (Peterson 2010). It is assumed that
this trend will be reversed and all future
fireline construction will conform to Forest
Plan standards and guides.
The proposed road work (resurfacing, culvert
replacement, etc.) would potentially benefit
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the dragonfly, as some of the culverts to be
replaced are contributing sediment to streams.
Improving leadoff ditches and other water
management structures would also reduce soil
movement.
The proposed temporary road construction
would involve removal of some overstory
trees, but would not result in the clearing of
large acreages that could be detrimental to
adult dragonflies. These roads would be
obliterated or revegetated upon completion of
thinning, elimination the potential for soil
movement from them.
Control of nonnative invasive plant species
would involve efforts targeted at individual
plants, rather than large-scale clearing efforts
that could expose large expanses of soil.
Thus, there would be little or no chance of
erosion and subsequent deposition of
sediment into aquatic habitats.
Cumulative Effects
Forsythe Creek originates in c-114, running
the length of the compartment before exiting
onto private land. Crib Creek originates in c-
112 and then crosses private land before
entering c-113. Activities on private lands
north of c-113 could potentially impact larval
habitat on the Forest. Any activities on
private lands were likely more intensive than
the actions proposed on national forest land,
and likely had fewer measures in place to
protect riparian areas and control soil
movement. The actions proposed in this
alternative will have numerous measures in
place to protect water quality, and are
unlikely to have long-term negative effects on
dragonfly larvae or their habitat.
Downstream effects to aquatic habitats were
also considered. Streams in these two
compartments ultimately flow into Alabama
Creek, which is on private land and feeds into
the Neches River. Management practices on
national forest lands incorporate measures
that minimize sediment movement into
aquatic habitats, as previously described.
These measures have not been fully
implemented in the past with regard to fireline
construction, resulting in degradation of
stream channels and banks, water quality, and
aquatic communities. It must be assumed that
there will be a commitment to fully
implement these measures for all future
firelines, as well as for all other soil-
disturbing activities. These measures reduce
the likelihood that the activities proposed
would negatively affect water quality
downstream of these compartments.
Similar work is being considered in the future
for other compartments in the Alabama Creek
WMA. Compartments 115 and 116 will be
the next compartments to be evaluated. These
two compartments do not lie in the watershed
of Lancaster and Crib Creeks and thus
activities in those compartments would not
contribute to effects experienced in those
creeks. However, compts. 115/116 do lie in
the larger Alabama Creek and Neches River
watersheds.
National forest land provides the best
opportunity for the protection or maintenance
of habitat for this species in the long-term.
Management practices near streams on
National Forest lands are generally more
restrictive than on adjacent private lands, on
which implementing protection measures for
streams is voluntary.
Fish, Freshwater Mussels, and Lotic
Crayfish - Affected Environment and
Environmental Consequences
Aquatic resources in Forsythe Creek in c-114
are presently relatively stable, except for
ongoing channel downcutting and sediment
delivery resulting from eroding firelines,
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failing culverts and uncontrolled road
drainage (Peterson 2010). Fisheries samples
from Alabama Creek, into which Forsythe
Creek empties, were rated fair to good in
1995, and considered representative of the
overall forest species assemblage (Peterson
2010).
While specific habitat requirements for the
fish, mussels, and crayfish differ, they are
primarily impacted by sedimentation.
Therefore, they are considered together in the
effects analysis.
Fish
3.8.3 Sabine Shiner (Notropis sabinae)
3.8.3.1 Environmental Baseline
The Sabine shiner has high potential to occur
over a substrate of fine, silt-free sand in small
streams and rivers having slight to moderate
current (Lee et al. 1980). Threats to this
species’ habitat include sedimentation and
obstructions to fish passage. Historic records
from 1968-1971 indicate that the Sabine
Shiner was originally found in a number of
streams on the NFT. There are no current
records of the species on the DCNF, although
it was found once and subsequently not
relocated.
However, the goldstripe darter (Etheostoma
parvipinne), a species closely associated with
the Sabine shiner, has been found in several
streams on the Forest. This species inhabits
clear, sandy bottom streams that are spring
fed. The goldstripe darter requires unimpeded
waterways that allow passage to headwaters,
needed for fulfilling life cycle requirements
and for survival during summer droughts.
Streams occupied by this species may indicate
the presence of habitat conditions necessary
to support the bottom dwelling Sabine shiner,
although recent findings indicate that the
shiner requires long reaches of streams, 13
miles or more, in order to thrive and support
sustainable populations. Impediments to fish
passage such as poorly designed and/or
placed culverts that impede passage to
headwaters are a major factor contributing to
the decline in distribution experienced by this
species.
The Sabine shiner does not have high
potential to occupy proposed treatment areas
because numerous previous inventories of
high potential habitat distributed across the
forest have not located this species.
Available Inventories
Numerous fisheries surveys and inventories
have been conducted on the DCNF. Table 3-
11 lists the most recent (since 1980)
inventory work.
Table 3-11. Fisheries inventory work on the Davy
Crockett National Forest since 1980.
Comp. Water
Body Date(s)
Sabine
Shiner
Found?
2 Austin
Branch
12/90,
1994,
1995
no
5
Pine
Spring
Creek
12/90,
5/97 no
5 Johnson
Creek
12/90,
12/95 no
11 Beaver
Creek 12/90 no
14 Beaver
Creek 7/97 no
15 Merkel
Creek 12/90 no
16 Pole
Branch
7/97,
8/98 no
17 Sandy
Creek
1994,
1995 no
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Chapter 3. Alternatives, Including the Proposed Action Page 37 of 52
Comp. Water
Body Date(s)
Sabine
Shiner
Found?
18 Camp
Creek
12/90,
1994,
1995,
10/95
no
19
Unnamed
branch off
Camp
Creek
3/99 no
24 Hickory
Creek
12/90,
1994,
1995
no
50 Hagar
Creek
1994,
1995 no
52 Cochino
Bayou
1994,
1995 no
54 Cochino
Bayou 10/98 no
54/57 Cochino
Bayou 1995 YES#
70 Lynch
Creek
1994,
1995 no
71 Piney
Creek 4 2/97 no
72 Piney
Creek 1 2/97 no
78 Armstrong
Creek 12/95 no
89 Caney
Creek 3/93 no
89
Upper
Caney
Creek
10/95 No
93 Piney
Creek 4/99 no
98 Piney
Creek
1994,
1995 no
110 Cedar
Creek 8/94 no
111 Hackberry
Creek
1994,
1995 no
Comp. Water
Body Date(s)
Sabine
Shiner
Found?
113 Alabama
Creek
1994,
1995,
fester
no
# Species not relocated in subsequent surveys
Available inventory information is adequate
because inventories of high potential habitat
on the DCNF are current enough and
widespread enough to guide project design,
support determination of effects, and meet
requirements for conservation of this species.
3.8.4 Freshwater Mussels
Sandbank Pocketbook (Lampsilis satura),
Louisiana Pigtoe (Pleurobema riddellii), and
Texas Heelsplitter (Potamilus
amphichaenus)
3.8.4.1 Environmental Baseline
Freshwater mussels may inhabit a variety of
water-body types including large and small
rivers and streams, lakes, ponds, canals, and
reservoirs (Howells et al. 1996). These three
sensitive mussel species have high potential
to occur in mud, sand, or gravel substrates in
streams and small rivers. They do not occur
in deep shifting sands or deep soft silt
(Howells 1996; Howells et al. 1996), which
can contribute to smothering. Mussels filter
feed on algae, detritus, and small particles in
the water, and may be able to absorb some
organic material in solution (Howells 1996).
Impoundment of river systems is believed to
be the most significant threat facing
freshwater bivalves (Neck 1982).
Impoundment alters flow regimes, increases
sediment accumulation, and may impede
movement of fish hosts. Dams may alter flow
and temperature regimes and disrupt the
timing of reproduction and associated
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behavior of fish and mussels (Neck 1982;
Howells et al. 1996). Pollution, over harvest,
reduced spring and river flows, introduction
of exotic species, and sedimentation are other
probable causes of decline (Neck 1982;
Howells 1996; Howells et al. 1996; Watters
2000). In addition, any impacts to fish may
negatively affect mussels, which use certain
fish as hosts for larval development (Howells
et al. 1996).
These species do not have high potential to
occupy proposed treatment areas because
previous inventories of high potential habitat
in streams distributed across much of East
Texas have not located these species in recent
years.
Available Inventories
Howells et al. (1996) summarized surveys
completed for these species in Texas. Only
two live specimens of the Texas heelsplitter
have been found in the past 15 years, and
none of the other two species. Texas
freshwater mussel communities have declined
greatly, and have disappeared from the
majority of sites from which they once were
found.
Available inventory information is adequate
because inventories of high potential habitat
are current enough and widespread enough to
guide project design, support determination of
effects, and meet requirements for
conservation of these species.
Lotic Crayfish
Blackbelted Crayfish (Procambarus
nigrocinctus)
Crayfish can be divided into two groups: 1)
those that live in lentic habitats (still waters
such as lakes, ponds, and swamps) and 2)
those that live in lotic habitats (actively
moving water such as streams and rivers).
The Neches crayfish and Sabine fencing
crayfish primarily inhabit lentic habitats and
will be addressed separately. The blackbelted
crayfish lives primarily in lotic environments,
and will be addressed along with other stream
dwelling species.
The blackbelted crayfish has high potential to
occur among debris in streams with sandy or
rocky bottoms, and is known from only five
locations range-wide, all in the Neches River
basin, in Angelina and Jasper counties (Hobbs
1990, p.581; Natureserve 2009). Activities
that negatively impact water quality have the
potential to impact this species.
Available Inventories
Crayfish surveys have been conducted at a
number of sites across the forest. Table 3-12
(below) summarizes those surveys.
Table 3-12. Crayfish inventory work on the Davy
Crockett National Forest
Comp. Water
Body Date(s)
P.
nigrocinctus
Found?
5
Spring
Creek at
FS 524
5/97 no
16
Camp
Creek at
FS 527
5/02 no
17
Sandy
Creek at
FS 511
4/01 no
18
Camp
Creek at
FS 511
4/01 no
19
Bluff
Creek at
FS 511
4/01 no
41
Piney
Creek at
FM 2781
5/01 no
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Comp. Water
Body Date(s)
P.
nigrocinctus
Found?
51
Hager
Creek at
FS 527
5/02 no
54
Bushy
Creek at
CR 4740
5/00 no
56 Pond off
FS 503B 10/03 no
56
Pond 5 –
503 past
plantation
4/04 no
71 Lynch
Creek
5/01,
4/03
YES
YES
78
Armstrong
Creek at
FS 527
5/02 no
78
Armstrong
Creek at
Ivie Spr.
off 596
12/95 no
92/93
Piney
Creek at
SH 94
5/02 no
Available inventory information is adequate
because inventories of high potential habitat
on the DCNF are current enough and
widespread enough to guide project design,
support determination of effects, and meet
requirements for conservation of this species.
Due to possible downstream impacts to water
quality, the cumulative effects analysis area
for these species includes streams in adjacent
compartments and private lands that flow into
the analysis areas, as well as downstream
areas in adjacent compartments and on private
lands.
3.8.4.2.1 Alternative 1 (no action)
Direct and Indirect Effects
Because no management actions would occur
under this alternative, no direct effects would
occur to these aquatic species. However, this
alternative would increase the vulnerability of
pine stands to wildfire and beetle infestation
(Turchin et al. 1999; Boyle et al. 2004).
Wildfire, depending upon intensity, could
remove riparian vegetation, including the root
mat, which functions to stabilize soil. If
increased sediment loads were delivered to
streams, particularly after heavy rain storms,
water quality could be negatively impacted,
potentially affecting any Sabine shiners,
crayfish, or mussels that might be present. If
no large wildfire, or wildfire near streams,
occurred, there would be no impact to aquatic
species as a result of this alternative.
Large, epidemic-level beetle infestations, and
the likely subsequent removal of dead and
dying pines, could result in the loss of large
acreages of forest cover. This could lead to
some temporary increases in sediment
delivery to streams, although protection
measures n the Forest Plan (USFS 1996)
would minimize this. However, it is difficult
to predict if, or when, this might occur. In the
absence of large-scale infestations, there
would be no impact on aquatic species.
Cumulative Effects
Existing ongoing erosion problems from past
firelines would begin to heal on their own,
although sedimentation would continue on
some sites. Without replacement, some
culverts would continue delivering sediment
to streams, further degrading stream quality
(Peterson 2010).
Disturbances to streams from private land
uses would continue because current
management practices are not expected to
change. Adjacent private lands possess few
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Chapter 3. Alternatives, Including the Proposed Action Page 40 of 52
areas of mature pine, and due to management
practices, are unlikely to provide high
potential habitat for aquatic species in the
future. Most adjacent private land has been
cleared for pasture land, and this trend is
likely to continue.
3.8.4.2.2 Alternative 2
Direct and Indirect Effects
Although timber removal and midstory
reduction would not occur within the primary
zone of MA-4, associated actions have the
potential to cause sediment movement.
Temporary stream crossings, in particular,
may increase sediment delivery to streams for
the short term. However, no long-term
adverse impacts to aquatic species are
anticipated from such crossings. Stream
crossings would be avoided, and alternative
routes used to access harvest units, whenever
possible. When in use, these crossings would
be used for a limited time and would be
identified and designated in accordance with
the Forest Plan (USFS 1996, p.158). Riparian
areas would be protected according to
measures outlined in the Forest Plan (USFS
1996, p.82-83, 153-154, and 158-159).
The thinning and midstory work proposed
under this alternative may result in temporary
increases in sediment delivery to streams.
However, long term adverse effects to stream
habitats are not anticipated. Silvicultural
activities rank low among water-impairing
land uses in the South (West 2002).
Prud’homme and Greis (2002) found that
scientific literature and monitoring results in
the south demonstrate that appropriate Best
Management Practices (BMPs), fully
implemented as designed and adapted to a
site, effectively protect water chemistry,
aquatic habitat, and aquatic biota. Forest Plan
measures and project design criteria are in
place for protecting stream courses (USFS
1996, p.82-83, 153-154, and 158-159). These
practices limit sediment delivery to streams,
and are consistent with, or more restrictive
than, state BMPs for protecting aquatic
habitats from sedimentation.
This proposal would involve prescribed
burning and the construction of fire lines.
The Sabine shiner, the mussels, and the
crayfish are vulnerable to management
actions that impact stream habitats. A major
problem associated with prescribed fire and
water quality is potential increases in
sedimentation (Stanturf et al. 2002).
However, most studies in the south indicate
that effects of prescribed fire itself on water
quality are minor and of short duration when
compared with the effects of other forest
practices (Stanturf et al. 2002). Prescribed
fires in MA-4 tend to consist of low intensity
backing fires. Even intense burns may disturb
the root mat very little, leaving its soil-
holding properties intact (Stanturf et al.
2002).
Fire lines constructed near streams are to be
constructed by hand within the 50 foot-wide
primary zone, minimizing soil disturbance
and the extent of sediment movement. If this
direction is followed, there would be little
potential for indirect effects to aquatic habitat,
provided that these hand lines are constructed
so as to prevent or minimize sediment
delivery to streams. However, past fireline
construction on the DCNF has not followed
standards and guides in the Forest plan (USFS
1996) designed to protect streams and
soil/water (Peterson 2010). It is assumed that
this trend will be reversed and all future
fireline construction will conform to Forest
Plan standards and guides.
No activities are proposed that could
potentially restrict fish passage along streams.
The proposed road work (resurfacing, culvert
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Chapter 3. Alternatives, Including the Proposed Action Page 41 of 52
replacement, etc.) would benefit aquatic
species, as some of the culverts to be replaced
are contributing sediment to streams.
Improving leadoff ditches and other water
management structures would also reduce soil
movement.
The proposed temporary road construction
would involve removal of some overstory
trees, but would not result in the clearing of
large acreages. These roads would be
obliterated or revegetated upon completion of
thinning, eliminating the potential for soil
movement from them.
Control of nonnative invasive plant species
would involve efforts targeted at individual
plants, rather than large-scale clearing efforts
that could expose large expanses of soil.
Thus, there would be little or no chance of
erosion and subsequent deposition of
sediment into aquatic habitats.
Cumulative Effects
Forsythe Creek originates in c-114, running
the length of the compartment before exiting
onto private land. Crib Creek originates in c-
112 and then crosses private land before
entering c-113. Activities on private lands
north of c-113 could potentially impact
aquatic habitat on the Forest. Any activities
on private lands were likely more intensive
than the actions proposed on national forest
land, and likely had fewer measures in place
to protect riparian areas and control soil
movement. The actions proposed in this
alternative will have numerous measures in
place to protect water quality, and are
unlikely to have long-term negative effects on
aquatic species or their habitat.
Downstream effects to aquatic habitats were
also considered. Streams in these two
compartments ultimately flow into Alabama
Creek, which is on private land and feeds into
the Neches River. Management practices on
national forest lands incorporate measures
that minimize sediment movement into
aquatic habitats, as previously described.
These measures have not been fully
implemented in the past with regard to fireline
construction, resulting in degradation of
stream channels and banks, water quality, and
aquatic communities. It must be assumed that
there will be a commitment to fully
implement these measures for all future
firelines, as well as for all other soil-
disturbing activities. These measures reduce
the likelihood that the activities proposed
would negatively affect water quality
downstream of these compartments.
Similar work is being considered in the future
for other compartments in the Alabama Creek
WMA. Compartments 115 and 116 will be
the next compartments to be evaluated. These
two compartments do not lie in the watershed
of Lancaster and Crib Creeks and thus
activities in those compartments would not
contribute to effects experienced in those
creeks. However, compts. 115/116 do lie in
the larger Alabama Creek and Neches River
watersheds.
National forest land provides the best
opportunity for the protection or maintenance
of habitat for these species in the long-term.
Management practices near streams on
National Forest lands are generally more
restrictive than on adjacent private lands, on
which implementing protection measures for
streams is voluntary.
3.8.5 Lentic Crayfish - Affected
Environment and Environmental
Consequences
Neches Crayfish (Procambarus nechesae)
and Sabine Fencing Crayfish (Faxonella
beyeri)
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Chapter 3. Alternatives, Including the Proposed Action Page 42 of 52
3.8.5.1 Environmental Baseline
The Neches crayfish has high potential to
occur in simple burrows in temporary or
semi-permanent pools in roadside ditches
(Hobbs 1990, p.593, Natureserve 2010). This
species is associated with the Neches River
Basin (Hobbs 1990, p.595). The Sabine
fencing crayfish has high potential to occur in
roadside ditches that are intermittently filled
(Natureserve 2010). Limiting factors for
these crayfish include land development or
alterations, agricultural runoff, and
competition with other crayfish (Natureserve
2010). Heavy equipment used during timber
operations has the potential to entomb
crayfish in burrows, compact the soil, and
affect hydrology through rutting.
Available Inventories
Numerous crayfish surveys and inventories
have been conducted on the DCNF. Table 2
(above) lists the most recent (since 1980)
inventory work. F. beyeri has not been found
on the DCNF. P. nechesae has been found at
one location, Pond 5 on FS 503, in C-56.
Available inventory information is adequate
because inventories of high potential habitat
on the DCNF are current enough and
widespread enough to guide project design,
support determination of effects, and meet
requirements for conservation of these
species.
3.8.5.2.1 Alternative 1 (no action)
Direct and Indirect Effects
Because no management actions would occur
under this alternative, no direct effects would
occur to these aquatic species. However, this
alternative would increase the vulnerability of
pine stands to wildfire and beetle infestation
(Turchin et al. 1999; Boyle et al. 2004).
Wildfire, depending upon intensity, could
remove riparian vegetation, including the root
mat, which functions to stabilize soil. If
increased sediment loads were delivered to
streams ditches, and ephemeral pools,
particularly after heavy rain storms, water
quality would be negatively impacted,
potentially affecting any crayfish that might
be present. If no large wildfire, or wildfire
near streams, occurred, there would be no
impact to these species as a result of this
alternative.
Large, epidemic-level beetle infestations, and
the likely subsequent removal of dead and
dying pines, could result in the loss of large
acreages of forest. This could result in some
temporary increase in sediment delivery to
streams, although protection measures n the
Forest Plan (USFS 1996) would minimize
this. Additionally, the use of heavy
equipment to remove dead and dying trees
could injure or kill some crayfish. However,
it is difficult to predict if, or when, this might
occur. In the absence of large-scale
infestations, there would be no impact on
aquatic species, since no actions would occur
in these two compartments.
3.8.5.2.2 Alternative 2
Direct and Indirect Effects
The proposed thinning and midstory reduction
using mechanical equipment would involve
the use of heavy equipment, which has the
potential to injure or kill individual crayfish if
it crosses wet ditches containing crayfish, or
drives over their burrows. However, these
species would be most likely to occur in
wetter sites such as roadside ditches, as
described above. These areas would be most
likely be impacted at only a few sites, where
equipment entered compartments. Thus,
impacts on those sites potentially harboring
the greatest numbers of crayfish would be
limited.
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Chapter 3. Alternatives, Including the Proposed Action Page 43 of 52
This proposal would involve prescribed
burning and the construction of fire lines.
The prescribed burning itself would not affect
these crayfish, since they would either be in
wet ditches or below ground in burrows. The
use of bulldozers to develop firelines has
potential to injure or kill individuals, if this
equipment crosses wet ditches containing
crayfish, or drives over their burrows.
However, equipment would not be making
numerous crossings of such areas; rather, only
a few crossings would be needed into each
compartment, and these may or may not
coincide with sites occupied by crayfish.
Thus, while there is the potential for some
individuals to be impacted, the impacts to the
species’ potential distribution would be small.
The proposed road work (resurfacing, culvert
replacement, etc.) would potentially benefit
these species. Improving leadoff ditches and
other water management structures would
reduce soil movement, which could benefit
crayfish inhabiting ditches and other low-
lying areas.
The proposed temporary road construction
would involve removal of some overstory
trees, but would not result in the clearing of
large acreages that could result in sediment
movement.
Control of nonnative invasive plant species
would involve efforts targeted at individual
plants. These efforts would thus not
contribute to sediment delivery to streams,
ditches, or temporary pools.
Cumulative Effects
The use of heavy equipment on national forest
land for fireline construction, timber harvest,
mechanical midstory reduction, roadwork,
and other activities has the potential to impact
these species and their temporary wet sites
across the forest. However, with the
exception of the need for bulldozers to cross
ditches to access fireline locations, and road
construction across ditches, other activities
typically avoid wet areas, or are restricted
seasonally to drier times of the year. This
reduces the potential for impacts to habitat for
these species, since during dry times they are
likely less widely distributed, likely being
concentrated in the fewer wet areas. In
addition, the activities discussed above occur
at the level of the individual, and generally do
not destroy the habitat.
Activities on surrounding private lands are
much less regulated, and effects on seasonally
wet sites, ephemeral pools, etc. can be
extensive, and may render sites uninhabitable.
This makes national forest land important for
the continued existence of these species.
3.9 Management Indicator Species (MIS)
The management indicator (MI) approach is
designed to help indicate the effects of
management on biological resources. The
analysis of MI represents a broad evaluation
of biological resources and effects of
management at the level of the entire NFGT,
and is intended to guide decisions about the
need to change management direction at this
broad level, while providing useful context
for project development and effects analyses
(USFS 2007, Appendix A, p.1).
Management indicators are identified in the
Revised Land and Management Plan for the
National Forests and Grasslands in Texas (the
Plan, p.306-307). Management indicator
species (MIS) are addressed in order to
implement NFMA regulations. MIS are
selected because their population changes are
believed to indicate the effects of
management activities. MIS include: species
with special habitat needs; species commonly
hunted, fished or trapped; non-game species
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Chapter 3. Alternatives, Including the Proposed Action Page 44 of 52
of special interest; and plant and animal
species whose population changes are
believed to indicate the effects of
management activities on other species,
groups of species, or selected communities.
For this project, a subset of the NFGT-wide
list of management indicators was selected.
Three species (Eastern wild turkey, yellow-
breasted chat, and pileated woodpecker) were
selected based upon their associations with
the habitat present in the analysis area and
their suitability as indicators of habitat
changes brought about by the proposed
alternatives (See Appendix II for an attached
list of those MI considered and those that
were eliminated from further consideration
and the rationale therein).
Management Indicator Species
Birds
Eastern wild turkey (Meleagris gallopavo)
Yellow-breasted chat (Icteria virens)
Pileated woodpecker (Dryocopus pileatus)
Birds - Affected Environment and
Environmental Consequences
3.9.1 Eastern Wild Turkey (Meleagris
gallopavo)
3.9.1.1Background and Current Status
Eastern wild turkeys require a diversity of
habitats in order to thrive, and will use
different habitats during different life cycle
stages. Nesting habitat typically has dense
herbaceous vegetation, with some shrubs and
some type of structure concealing the nest.
Nest sites are often placed near openings or
edges such as roads, pastures, young
plantations, or similar sites (Hurst and
Dickson 1992). Brood habitat, particularly
for young broods up to 10 days old, is
especially important. Young poults forage
heavily on insects, and need open areas with
abundant herbaceous vegetation and
associated insects (Healy and Nenno 1983;
Healy 1985; Campo et al. 1989; Hurst and
Dickson 1992; Porter 1992). Wintering
flocks make heavy use of hardwood stands,
particularly bottomland areas (Sisson et al.
1990; Hurst and Dickson 1992).
Openings are an important habitat component
year around, and are used as strutting areas by
gobblers (Hurst and Dickson 1992), as
bugging areas by hens with broods (Healy
1985; Campo et al. 1989; Hurst and Dickson
1992), and as foraging areas by turkeys of all
ages throughout the year (Hurst and Dickson
1992). A study in Louisiana found that areas
with a larger percentage of acreage in
openings usually had higher turkey
populations (Dickson et al. 1978).
Turkeys have a varied diet. As previously
mentioned, young poults are heavily
dependent on insects, transitioning to a more
plant-dominated diet by four weeks of age
(Healy and Nenno 1983; Healy 1985; Hurst
1992). Adult turkeys feed primarily on plant
foods, including seeds, hard mast such as
acorns and nuts, soft mast such as fruits and
berries, and green vegetation. They also
consume some animal matter, primarily
insects (Hurst 1992). Good turkey habitat
provides a diversity of foods and habitats to
satisfy the needs of turkeys during their
different life stages.
The eastern wild turkey was selected as a
management indicator because it is in demand
by hunters and because it responds well to
changes in habitat quality. The objective is to
increase turkey populations on the National
Forests and Grasslands in Texas.
Turkey numbers were tracked by TPWD
through brood surveys, but this technique was
discontinued in 2005. New monitoring
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Chapter 3. Alternatives, Including the Proposed Action Page 45 of 52
techniques are being evaluated, and will be
implemented on a larger scale if they provide
adequate population information (USFS 2007,
Appendix A, pp. 8 & 10). Prior to being
discontinued, brood surveys showed a general
declining trend across the NFGT through
2002 (Fig. 1; USFS 2005).
Fig. 3-3. Number of Eastern wild turkeys counted
during annual brood surveys by Texas Parks and
Wildlife Department in counties where National
Forests and Grasslands are located. (NFGT M&E
Report 2002-2003, Appendix F).
NFT-wide turkey population trends are
presently tracked in part through spring
hunter harvest data. Figure 2 (USFS 2007,
Appendix A, p. 9) shows the number of
turkeys harvested in 12 counties containing
National Forest lands, and suggest a fairly
stable trend NFT-wide.
Fig.3-4. Spring turkey harvest (# of turkeys) in
Angelina, Houston, Jasper, Nacogdoches, Newton,
Sabine, San Augustine, Shelby, San Jacinto, Trinity,
Montgomery, and Walker Counties, 1997 – 2006
(USFS 2007, Appendix A, p. 9).
Harvest on the DCNF has increased in recent
years (Fig. 3), perhaps suggesting that turkey
numbers may be increasing in some parts of
the Forest.
Fig. 3-5. Turkey harvest on the Davy Crockett
National Forest, 1997 – 2008 (TPWD 2007).
Declines on NFT are likely due to habitat
deterioration from lack of adequate prescribed
burning, particularly from 2000-2003. The
loblolly forest type rapidly becomes choked
with woody understory species such as
yaupon, wax myrtle, and sapling hardwoods
in the absence of frequent fire, quickly
rendering it unsuitable for turkeys. However,
the burning program increased in 2004, and
continued increases are planned. This should
help the turkey population across the National
Forests and Grasslands in Texas.
0
200
400
600
800
1000
1200
1994 1996 1998 2000 2002
Turkeys
0
10
20
30
40
50
60
70
80
90
1997 1999 2001 2003 2005
Harvest
0
2
4
6
8
10
12
1997 2000 2003 2006
Harvest
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Chapter 3. Alternatives, Including the Proposed Action Page 46 of 52
The cumulative effects analysis area for this
species consists of compts. 113 and 114, the
remainder of the Alabama Creek WMA
(compts. 112 and 115-121), and surrounding
private lands.
3.9.1.2.1 Alternative 1 (no action)
Direct and Indirect Effects
There would be no direct effects on the
eastern wild turkey, because no actions would
occur under this alternative.
Alternative 1 would indirectly affect habitat
suitability and foraging quality and quantity
for the turkey. Neither compartment
presently provides high quality habitat for
turkeys due to the rather extensive hardwood
midstory. This midstory, in addition to the
high basal area of the pine stands, restricts
sunlight from reaching the forest floor in
many areas, thus inhibiting growth of
herbaceous vegetation. Failure to adequately
manage these compartments would limit
turkey use of these areas, and would not
contribute to growth of the Davy Crockett
turkey population.
Cumulative Effects
Turkey habitat in the analysis area would
remain marginal or poor without management
actions. Habitat on private lands is limited for
this species. Most surrounding private land is
in pasture and unmanaged woodlots. This
land does provide some open areas for turkeys
immediately adjacent to the Forest, but
turkeys are not likely to use pastures distant
from the Forest. Private forested land is not
being managed to provide the open, grassy
understories that turkeys need, and generally
has thick brushy understories. Management
practices on these lands are unlikely to
produce good quality habitat that would
sustain this species in the future.
3.9.1.2.2 Alternative 2
Direct and Indirect Effects
Potential direct effects of this alternative
include the displacement of individual
turkeys, death or injury of poults, or the loss
of nests from the proposed activities, should
any turkeys be present in the treatment areas
and depending on the season in which
activities occur. Hens with nests damaged or
destroyed will often re-nest. Although these
actions may impact individuals, the thinning,
prescribed fire, and midstory reduction offer
the greatest opportunity for developing or
improving habitat for turkeys in these two
compartments.
Indirect effects would be beneficial to the
turkey. The pine and hardwood thinning,
coupled with the midstory reduction work,
would create more open stand conditions.
Prescribed fire would further reduce the
amount of woody understory vegetation and
stimulate germination of grasses and forbs.
The more open canopy resulting from
thinning would increase available light to the
forest floor, which would further promote the
establishment or expansion of herbaceous
ground cover. The resulting habitat could be
used as cover by nesting hens and for
foraging by poults. The proposed 2-5 year
burning interval would likely maintain
moderately open understories.
An average of 3-10 site-appropriate
hardwoods > 5” dbh would be retained per
acre during thinning and midstory reduction.
Prescribed burning is unlikely to harm large,
upland hardwoods and the other site-
appropriate species that would be retained. A
loss of hardwoods from fire in or near riparian
areas would be negligible, due to low fire
intensity in these areas. No thinning or
midstory reduction would occur in the
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Chapter 3. Alternatives, Including the Proposed Action Page 47 of 52
primary zones of streams, so no hardwoods
would be removed in those areas.
The proposed road work (resurfacing, culvert
replacement, etc.) would not impact turkeys,
as it would not alter turkey habitat.
Construction of temporary roads would
provide linear openings which turkeys would
likely use for travel and for bugging. Closure
of these roads after completion of thinning
would preclude their illegal use by vehicles.
Turkeys would still use these roads as linear
openings until they closed in with sapling
trees.
Control of nonnative invasive plant species
would involve efforts targeted at individual
plants. NNIS are not major turkey food
sources, and in many cases they may in fact
crowd out more desirable native food species.
Thus, control may in some areas benefit
turkeys by allowing for establishment of
native food sources.
Cumulative Effects
Management practices on most adjacent and
nearby private lands currently do little to
enhance habitat for this species. Turkeys may
use the edges of pastures adjacent to the
Forest. Future sustainability or growth of
wild turkey populations in the vicinity will
depend largely on habitat developed or
maintained on national forest and state lands.
The thinning, midstory reduction, and
prescribed burning proposed under this
alternative would improve nesting and brood
habitat conditions, which would benefit the
eastern wild turkey.
Future projects are planned in other
compartments in Alabama Creek WMA, with
compts.115 and 116 being the next
compartments to be considered for treatments
similar to those proposed for compartments
113 and 114. This future work would build
on work completed in Compartments 113 and
114, creating a larger block of good quality
habitat better able to support a viable turkey
population.
3.9.2 Yellow-breasted Chat (Icteria virens)
This species is an indicator of early
successional habitat. The chat prefers
blackberry tangles, dense shrub thickets, and
scattered saplings interspersed among dense
herbaceous cover. Nests are generally located
in dense vegetation less than 2 m above
ground (NatureServe 2010). The yellow-
breasted chat has experienced significant
population declines in eastern North America
due to loss of habitat from the re-growth of
cleared forests, and the clearing of early
succession landscapes for agriculture and
urban development (Cornell Lab. of
Ornithology 2000).
Data are available to evaluate chat population
trends at several scales. Data from Breeding
Bird Survey routes, which have been operated
since 1966, provide information on yellow-
breasted chat population trends across the
species’ range (Fig. 4; Sauer et al. 2007).
These data reveal that chat populations have
fared differently in various parts of the U.S.
However, in much of the West Gulf Coastal
Plain, including the pineywoods of East Texas
and western Louisiana, the species has
averaged an increase of over 1.5% per year.
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Chapter 3. Alternatives, Including the Proposed Action Page 48 of 52
Fig. 3-6. Changes in yellow-breasted chat
populations across the species’ range, based upon
Breeding Bird Survey data (1966-2003). Map from
Sauer et al. (2007).
State rankings in Texas indicate the
populations are secure and stable
(NatureServe 2010). Available data gathered
from point count surveys on the NFT indicate
a relatively stable trend (Fig. 5; USFS 2007,
Appendix A, p. 15). These annual bird point
counts have been conducted on the four
Forests since 1998.
Fig. 3-7. Number of yellow-breasted chats detected
during point counts in all forest stands (USFS 2007,
Appendix A, p. 15).
3.9.2.1. Alternative 1 (no action)
Direct and Indirect Effects
There would be no direct effects on the
yellow-breasted chat because no new actions
would occur under this alternative.
There would be few indirect effects on chats.
Lack of thinning and midstory reduction
would leave the existing canopy in place.
Prescribed fire to date has created a fairly
open understory in many areas of the two
compartments. Chat habitat is not abundant
in the two compartments. No new early
successional habitat would be created under
this alternative.
Cumulative Effects
Few of the management practices currently
being practiced on nearby private lands are
compatible with developing or maintaining
chat habitat. Much of the private land
surrounding compartments 113 and 114 is in
pastureland, which does not provide habitat
for this species. There are some areas in
forest, which may support some chats, but
management of these stands varies. Because
of the extensive pastureland in the area, most
chat habitat will remain on national forest
land.
3.9.2.2 Alternative 2
Direct and Indirect Effects
The proposed thinning and midstory reduction
may displace individual chats or destroy some
nests. However, chats, like many songbirds,
usually renest. Nest losses from prescribed
burning would likely be minimal since
burning is typically already completed before
the main nesting period of mid-May through
June or July.
Indirect effects would be mixed for chats.
Thinning of both mature and younger stands
would open the overstory and increase light
penetration, potentially increasing growth of
woody understory vegetation. However,
0
50
100
150
200
250
300
1998 2000 2002 2004 2006
YBCH
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Chapter 3. Alternatives, Including the Proposed Action Page 49 of 52
continued prescribed burning would control
sprouting and growth of much of the woody
understory, encouraging development of a
grassy, herbaceous groundcover. The patches
that burned less intensely would provide
nesting habitat for chats for several years
between burns.
The proposed road work (resurfacing, culvert
replacement, etc.) would not impact chats, as
it would not alter chat habitat.
The linear openings created by temporary
roads would increase sunlight penetration to
the forest along the roads, stimulating woody
understory growth. However, they could also
serve as avenues for brown-headed cowbirds
to search for nests to parasitize, and they
could potentially reduce nest success of chats
nesting along the roads. However, these
roads would be revegetated after completion
of thinning, so any negative effects would be
temporary.
Control of nonnative invasive plant species
would involve efforts targeted at individual
plants. This activity would not affect chats,
because these NNIS are not major food or
cover sources for chats, and in many cases
they may in fact crowd out more desirable
native species.
Cumulative Effects
The thinning and prescribed burning proposed
under this alternative, and other similar
projects across the forest, would reduce the
vulnerability of pine-dominated stands to
wildfire and SPB infestation. Reducing pine
loss to potentially stand-replacing beetle
infestations could potentially result in fewer
acres of early sucessional habitat. As this
habitat type declines on the forest,
populations of yellow-breasted chats are also
expected to decline (USFS 2004, Appendix F,
p.15). However, based on point count
surveys, this species occurs widely across the
NFGT. Substantial acres of habitat, with
varying densities of woody understory
vegetation, would continue to exist
throughout the forest.
Adjacent private land may provide some early
successional habitat for this species on the
areas managed for short-rotation timber
production. However, much of the private
land near c-113/114 has been cleared for
pastureland.
3.9.3 Pileated Woodpecker (Dryocopus
pileatus)
The pileated woodpecker is an indicator of
mid and late succession and old growth
habitats. Preferred habitat includes mature
coniferous-deciduous forests or bottomland
hardwood forests. Pileated woodpeckers are
dependent on the availability of large snags
for foraging, roosting, and nesting.
Data are available to evaluate pileated
woodpecker population trends at several
scales. Data from Breeding Bird Survey
routes, which have been operated since 1966,
provide information on pileated woodpecker
population trends across the species’ range
(Fig. 6; Sauer et al. 2007). These data reveal
that pileated populations have fared
differently in various parts of the U.S.
However, in much of the West Gulf Coastal
Plain, including the pineywoods of East
Texas, the species has averaged an increase of
0.25% - 1.5% per year. This is likely due to
the continued aging of the pine forests.
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Chapter 3. Alternatives, Including the Proposed Action Page 50 of 52
Fig. 3-8. Changes in pileated woodpecker
populations across the species’ range, based upon
Breeding Bird Survey data (1966-2003). Map from
Sauer et al. (2007).
Point count surveys have been used on the
NFT to monitor pileated woodpecker numbers
since 1998. Available data indicate trends in
pileated woodpecker numbers are stable to
increasing across the four Forests (Fig. 7;
USFS 2007, Appendix A, p. 17), similar to
the trend documented by breeding bird survey
data. Given the trend since 1998, the
apparent large drop in numbers for 2006 is
likely an anomaly; future counts will provide
an answer.
Fig. 3-9. Number of pileated woodpeckers detected
during point counts in all forest stands (USFS 2007,
Appendix A, p. 17).
Habitat for this species, in the form of older
age forest stands, is increasing across the
national forests in Texas (Table 13; USFS
2007, Appendix A, p. 5). As the forest
continues to age, pileated woodpeckers would
find improved habitat conditions in the form
of larger diameter trees and more decadent
trees in which to excavate cavities.
Seral
Stage Age 1992 2002 2004 2006 Trend
Early
0-
20
yrs
22% 14% 13% 11% -
11%
Mid
21-
50
yrs
11% 15% 15% 17% +6%
Late
51-
90
yrs
61% 55% 53% 50% -
11%
Very
Late
91+
yrs 6% 16% 18% 22%
+16
%
Table 3-13. Percentage of National Forest lands in
each seral stage from 1992-2006, and percent
change since 1992 (USFS 2007; Appendix A, p. 5).
3.9.3.1 Alternative 1 (no action)
Direct and Indirect Effects
There would be no direct effects on the
pileated woodpecker, because no actions
would occur under this alternative.
Indirect effects would be potentially mixed.
Pileated woodpeckers would benefit as stands
continue to develop and mature. As these
stands increased in density, they would
become more susceptible to individual tree
mortality from stress, or larger-scale mortality
from disturbances such as wildfire or SPB
infestation. This would result in the creation
of snags that could be used as foraging and
nest sites.
However, these densely-stocked stands would
also be more vulnerable to potentially stand-
replacing events such as large beetle
infestations, which could temporarily provide
an abundance of snags for foraging and
nesting, but could ultimately result in the loss
0
10
20
30
40
50
60
70
80
90
100
1998 2000 2002 2004 2006
PIWP
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Chapter 3. Alternatives, Including the Proposed Action Page 51 of 52
of forest cover on the affected area until
replanted trees matured sufficiently to again
provide a source of large snags.
Cumulative Effects
Adjacent private land uses generally do not
support the retention of large areas of mature
pine or hardwood forest, or the protection of
snags. Potential pileated woodpecker habitat
has been removed on much of the nearby
private land through conversion to
pastureland. National Forest lands ultimately
provide the best habitat for this species in this
area.
3.9.3.2 Alternative 2
Direct and Indirect Effects
Direct or inadvertent removal of snags and
downed logs may occur during project
activities. Thinning the mature stands would
result in increased vigor and reduce the
potential for beetle infestation and the
resultant loss of large acreages of mature
forest habitat. Thinning the younger stands
would decrease competition, resulting in
increased growth rates and shortening the
time until these stands began producing the
large-diameter snags needed by this species
for nesting.
Prescribed burning may consume some large
snags, but would likely create new snags,
depending upon the intensity of the burn.
Many prescribed fires burn hot enough in
some patches to kill occasional overstory
pines, which would provide ideal roost and
nest trees. According to Van Lear (1993),
prescribed fire results in both the loss and
production of snags. However, snags are
more frequent in lowlands and riparian zones
than on upland sites (Van Lear 1993).
Because fire tends to burn at low intensity in
riparian areas, it is unlikely to have negative
impacts on snags and downed logs in these
areas. Despite possible losses in upland areas,
large snags would continue to exist for the
pileated woodpecker.
The proposed road work (resurfacing, culvert
replacement, etc.) would not impact these
woodpeckers, as it would not alter their
habitat.
The proposed temporary road construction
may involve removal of some large trees.
However, the number removed would be
minimal when compared to the amount of
habitat present in the compartments, and thus
would not negatively affect the woodpecker.
Control of nonnative invasive plant species
would involve efforts targeted at individual
plants. The species to be treated do not
provide good foraging sites (large trees, large
dead and down material) for the woodpeckers.
This activity would not affect pileated
woodpeckers, because these NNIS do not
provide large the diameter snags needed for
nesting, and also do not provide foraging sites
for pileated woodpeckers.
Cumulative Effects
Thinning and prescribed fire would decrease
the chance of SPB infestation or a wildfire
that could possibly burn hot enough to kill
large areas of the overstory. This would
improve the likelihood that pine stands would
attain an older age class with a more uniform
and continuous supply of large snags.
Nearby compartments, beginning with c-115
and 116, will soon be evaluated for similar
treatments as those being considered for
compartments 113 and 114. Thus, a large
block of habitat may be thinned, and the risk
of large-scale beetle infestation reduced.
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Chapter 3. Alternatives, Including the Proposed Action Page 52 of 52
Adjacent private land uses generally do not
support the retention of large areas of mature
pine or hardwood forest, or the protection of
snags. Potential pileated woodpecker habitat
has been removed on much of the nearby
private land through conversion to
pastureland. National Forest lands ultimately
provide the best habitat for this species in this
area.
3.10 Public Health and Safety
3.10.1 Alternative 1 (No Action) Public health and safety would not be directly
affected. The potential for losses from
wildfire would increase over time due to
increased fuel loads and dense forest
conditions. This could indirectly affect public
health and safety, if wildfire occurred in
Compartments 113 and 114. Wildfires
produce much more smoke and pollutants
than prescribed fires, which could adversely
affect public health. In addition, wildfires can
be difficult to control, placing nearby
residents and firefighters at greater risk.
3.10.2 Alternative 2
Public health and safety would be minimally
affected. Measures to protect the public
during logging and prescribed burning would
be implemented. The potential for losses
from wildfire would decrease over time as
prescribed burning and timber harvesting
reduce fuel loads and create open forest
conditions. Prescribed fires produce less
smoke and pollutants than wildfires and
would be conducted when atmospheric
conditions promote the dispersal of smoke,
which would minimize the effects on public
health.
None of the alternatives present a risk to
human health and safety with the
implementation of mitigating measures to
restrict access during logging, prescribed
burning or other activities.
3.11 Economics
For proposed projects involving timber sales,
the Timber Sale Preparation Handbook,
directs economic or financial analyses be
conducted for all alternatives (FSH 2409.18).
For this project, the Davy Crockett ID Team
conducted a financial efficiency analysis for
Alternative 2. It should be noted that analysis
was limited to direct monetary costs and
revenues related to the timber sales. It does
not factor in non-monetary benefits of
improved forest health, improved wildlife
habitat, or reduced risk of wildfire damage.
Costs included: road maintenance, sale
administration, site preparation (marking),
prescribed burning, tree planting, survival
checks, and midstory removal. Benefits
included the revenue generated from the sale
of the timber. All monetary estimates were
based on recent actual values. Table 3-10
summarizes the results.
Table 3- 10. Economic efficiency of Alternative 2
Alt
ern
ati
ve 2
Discount Rate 4.000
Cash Flows (number) 28
PV – Costs ($) -$ 1,489,077.97
PV – Benefits ($) $ 2,501,501.00
Present Net Value ($) $ 1,003,423.03
B/C Ratio 1.67
Investment Length (years)
10
Net Annual Equivalent ($)
$ 123,712.97
Composite Rate of Return (%)
9.47
Generally, Alternative 2 would generate
several hundred thousand dollars more than it
cost. Implementation of Alternative 2 is
economically viable.