3.0 Affected Environment and...

Davy Crockett NF – Lancaster-Forsythe Project

Environmental Assessment Phase I – Compartment 113 & 114 – Crib & Forsythe Creek

Chapter 3. Alternatives, Including the Proposed Action 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




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




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

http://soils.usda.gov/technical/manual/print_version/chapter6.html




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




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.




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.



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,




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.


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




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


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




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.



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.


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,




essentially no differences exist between the

current conditions and Alternative 2 in terms

of expected annual emissions.

3.4 Recreation and Scenic Resources


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




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).



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.


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




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


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


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




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




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,




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




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.



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




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).


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




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)


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%




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




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).


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




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).




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




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).




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




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




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




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


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




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




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


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


3.8.1 Rafinesque's Big-eared Bat (Corynorhinus rafinesquii)


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)




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.


species consists of the two compartments

covered in this proposal, adjacent

compartments, and private lands surrounding

these national forest lands.


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.





occur to this bat species.




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.



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




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


3.8.2 Texas Emerald Dragonfly (Somatochlora margarita)


The Big Thicket emerald dragonfly has a

potential range that may exceed 10,000 square




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


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.


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.



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




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.



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.


replacement, etc.) would potentially benefit




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


Aquatic resources in Forsythe Creek in c-114

are presently relatively stable, except for

ongoing channel downcutting and sediment

delivery resulting from eroding firelines,




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)


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


because numerous previous inventories of

high potential habitat distributed across the

forest have not located this species.


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




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


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)


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




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.


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.



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.


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




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






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.





occur to these aquatic species. However, this

alternative would increase the vulnerability of

pine stands to wildfire and beetle infestation


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




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.



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.





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.




large acreages. These roads would be

obliterated or revegetated upon completion of

thinning, eliminating the potential for soil

movement from them.



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)





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.


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.






requirements for conservation of these

species.





occur to these aquatic species. However, this

alternative would increase the vulnerability of

pine stands to wildfire and beetle infestation


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.



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.




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.


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.




large acreages that could result in sediment

movement.



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




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


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




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





species consists of compts. 113 and 114, the

remainder of the Alabama Creek WMA

(compts. 112 and 115-121), and surrounding

private lands.



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.



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




primary zones of streams, so no hardwoods

would be removed in those areas.


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.



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.




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)



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.



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




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.


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.



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.




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)



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




of forest cover on the affected area until

replanted trees matured sufficiently to again

provide a source of large snags.

Cumulative Effects


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.



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.


replacement, etc.) would not impact these

woodpeckers, as it would not alter their

habitat.


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.



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.





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.

3.0 Affected Environment and...

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