ATTACHMENT_7_-_RCW_Recovery_Plan.pdf

Red-cockaded Woodpecker Recovery Plan ii

DISCLAIMER

This Recovery Plan Revision outlines the actions that, to the best of current understanding, are necessary to recover red-cockaded woodpeckers. It does not represent the view or official position of any individuals or agencies involved in the development of the plan, other than the U.S. Fish and Wildlife Service. It represents official policy of the U.S. Fish and Wildlife Service only after the regional director has signed it as approved. This revision is subject to further modification as dictated by new findings, changes in species status, and completion of recovery tasks. Implementation of this plan is the responsibility of federal and state management agencies in the areas where the species occurs. Implementation is done through incorporation of management guidelines identified within this Recovery Plan Revision into agency decision documents. Decision documents, as defined by the National Environmental Policy Act (NEPA), are subject to the NEPA process for public review and alternatives selection.

LITERATURE CITATION SHOULD READ AS FOLLOWS:

U.S. Fish and Wildlife Service. 2003. Recovery plan for the red-cockaded woodpecker

(Picoides borealis): second revision. U.S. Fish and Wildlife Service, Atlanta, GA. 296 pp.

ADDITIONAL COPIES MAY BE PURCHASED FROM:

Fish and Wildlife Reference Service 5430 Grosvenor Lane, Suite 110 Bethesda, MD 20814

(301) 492-6403 or (800) 582-3421

Fees for documents vary depending on postage and number of pages.

STANDARD ABBREVIATIONS

The following standard abbreviations for units of measurement are found throughout this document:

cm = centimeters in = inches m2 = square meters m = meters ft = feet ft2 = square feet km = kilometers mi = miles dbh = diameter at breast height ha = hectares ac = acres g = grams oz = ounces

Red-cockaded Woodpecker Recovery Plan iii

ACKNOWLEDGMENTS

The process of revising the 1985 red-cockaded woodpecker recovery plan began in August 1995, when potential recovery team members were identified. In January 1996, 15 potential members were asked to participate on the team; all accepted. The first team meeting was held in March 1996; two additional meetings, each one week long, were held in April and December 1997. Between March 1996 and March 2000, team members individually spent hundreds of hours working on the revision, including participation in team meetings, writing, and reviewing. The U.S. Fish and Wildlife Service is very appreciative of the time and hard work put forth by team members during this process. Combined, the team has approximately 257 years of red-cockaded woodpecker experience in the private, state, and federal sectors. Their professional experiences with red-cockaded woodpeckers have included research, population and habitat management, and regulatory and policy responsibilities. They have unselfishly contributed their knowledge, time, and expertise to the many challenges of the recovery plan revision process. The U.S. Fish and Wildlife Service thanks each of them for their contributions and is grateful to have worked with such a team.

By April 1999, much of the Introduction had been drafted. However, several major tasks remained to be accomplished. These tasks included writing Recovery, Listing, Executive Summary, and other sections; compiling and editing the contributions of 15 other authors; and creating tables, Literature Cited, and Index. In April 1999, the U.S. Fish and Wildlife Service hired Ms. Susan Daniels as a wildlife biologist and recovery team member to take the lead on completing these tasks. The recovery team and U.S. Fish and Wildlife Service are proud to extend special thanks to “one of our own” for her continuous hard work during the past four years on this challenging project.

Sue has done an outstanding job of assembling and completing this revision.

Ultimately, recovery of the red-cockaded woodpecker is and will be dependent upon the on-the-ground hard work of biologists, foresters, technicians, researchers, and land managers working on the private, state, and federal properties where the birds survive. During the past seven years, many of these individuals have been asked to supply information including population and habitat data, maps, and management costs.

The U.S. Fish and Wildlife Service and the recovery team are particularly grateful to these many individuals for their timely and reliable responses to our requests. They have supplied a tremendous amount of information for this document.

Red-cockaded Woodpecker Recovery Plan Table of Contents iv

TABLE OF CONTENTS

ACKNOWLEDGMENTS ............................................................................................... III TABLE OF CONTENTS................................................................................................ IV EXECUTIVE SUMMARY.............................................................................................. IX

CURRENT STATUS ...................................................................................................IX BASIC ECOLOGY AND POPULATION DYNAMICS ........................................................IX HABITAT REQUIREMENTS AND LIMITING FACTORS....................................................X POPULATION AND SPECIES VIABILITY ......................................................................XI RECOVERY GOAL ...................................................................................................XII RECOVERY CRITERIA .............................................................................................XII

Delisting................................................................................................................................................. xiii Rationale for Delisting Criteria.................................................................................................................xiv Downlisting ..............................................................................................................................................xv Rationale for Downlisting Criteria ............................................................................................................xvi

ACTIONS NEEDED ................................................................................................ XVI DATE OF RECOVERY............................................................................................ XVII

PART I. INTRODUCTION

1. LISTING

A. REASONS FOR LISTING

Loss of the Original Ecosystems Fire Suppression Detrimental Silvicultural Practices

B. CURRENT THREATS

2. GENERAL BIOLOGY AND ECOLOGY

A. TAXONOMY AND SPECIES DESCRIPTION

B. SOCIOBIOLOGY AND COOPERATIVE BREEDING

The Breeding System Reproduction Mortality Population Dynamics

C. POPULATION AND SPECIES VIABILITY

Population Structure Threats to Population Viability A Strategy for Species Viability

D. CAVITIES, CAVITY TREES, AND CLUSTERS

Cavity Excavation and Selection of Cavity Trees The Cavity Tree Cluster Cavity Tree Mortality and Protection Implications for Management

E. FORAGING ECOLOGY

Diet and Prey Abundance Selection of Foraging Habitat Home Range and Habitat Quality Group Fitness and Habitat Quality Geographic Variation in Foraging Habitat Previous Management Guidelines Implications for New Management

F. COMMUNITY ECOLOGY:

CAVITY KLEPTOPARASITISM, CAVITY ENLARGEMENT, AND PREDATION

Cavity Kleptoparasitism Cavity Enlargement Predation v

Indirect Interactions Implications for Management

G. THE ROLE OF FIRE IN SOUTHERN PINE ECOSYSTEMS

History of Fire in the Southeast Fire Dependence and Adaptation Implications for Management

3. MANAGEMENT TECHNIQUES

A. POPULATION MONITORING

Population Size and Trend Translocation Evaluating other Management Actions Evaluating Impacts of Activities other than Species Management Mitigation Monitoring Research Monitoring Annual Reporting of Monitoring Results

B. CAVITY MANAGEMENT: ARTIFICIAL CAVITIES AND RESTRICTOR PLATES

Artificial Cavities Restrictor Plates

C. PREDATOR AND CAVITY KLEPTOPARASITE CONTROL

Exclusion of Rat Snakes Exclusion of Southern Flying Squirrels Lethal vs. Non-lethal Methods of Control

D. TRANSLOCATION

Benefits and Drawbacks to Translocation History of Translocation of Red-cockaded Woodpeckers Translocation Success

E. SILVICULTURE

Silvicultural Systems Pine Density Priority for Leave Trees Site Preparation

F. PRESCRIBED BURNING

Benefits of Prescribed Burning Season of Prescribed Burning Application of Fire to the Landscape Restoration Burning and the Reintroduction of Fire

G. HABITAT RESTORATION

Restoration of Native Canopy Pines Restoration of Historic Pine Densities Restoration of Native Groundcovers

H. ECOSYSTEM MANAGEMENT

Ecosystem Management and Red-cockaded Woodpeckers

4. CURRENT STATUS AND CONSERVATION INITIATIVES

A. PRIVATE LANDS

The Endangered Species Act and Private Landowners Recent Trends and Current Status The Private Lands Conservation Strategy Mitigation Other Incentive Programs

B. STATE LANDS

Status and Distribution Recovery Role Conservation of Biodiversity within States

C. FEDERAL LANDS

National Forests Military Installations National Wildlife Refuges vi

Other Federal Lands

D. NATIVE AMERICAN TRIBAL TRUST LANDS

PART II. RECOVERY

5. RECOVERY GOAL

6. RECOVERY CRITERIA

A. DELISTING

Rationale for Delisting Criteria Delisting Criteria and Listing Factors Identified in the Endangered Species Act

B. DOWNLISTING

Rationale for Downlisting Criteria

7. RECOVERY UNITS

Recovery Units as the Basis for Jeopardy Analysis in Interagency Consultation Ecoregions Translocation Primary and Secondary Core Populations Support Populations Individual Recovery Units Gulf Coast Prairies and Marshes Ecoregion Mississippi Alluvial Plain

8. MANAGEMENT GUIDELINES

A. ASSESSING PROGRESS TOWARD RECOVERY

B. USE OF RECRUITMENT CLUSTERS

C. POPULATION MONITORING

D. HABITAT MONITORING

E. CAVITY MANAGEMENT, ARTIFICIAL CAVITIES, AND RESTRICTOR PLATES

F. CLUSTERS AND CAVITY TREES

G. PREDATORS AND CAVITY KLEPTOPARASITES

H. TRANSLOCATION

I. FORAGING HABITAT

Part A. Recovery Standard Part B. Assessment of Foraging Habitat

J. SILVICULTURE

Part A. General Guidelines for Silviculture Part B. Silvicultural Systems and Implementation of Foraging Guidelines

K. PRESCRIBED BURNING

9. RECOVERY TASKS

10. IMPLEMENTATION SCHEDULE AND ESTIMATED COSTS

LITERATURE CITED

GLOSSARY OF TERMS

INDEX

APPENDIX 1. PERMITS, TRAINING, AND COMPLIANCE REQUIREMENTS

APPENDIX 2. PROTOCOL FOR MONITORING REPRODUCTIVE SUCCESS, GROUP SIZE,

AND GROUP COMPOSITION (COLOR-BANDING)

APPENDIX 3. PROTOCOL FOR TRANSLOCATION EVENTS

APPENDIX 4. SURVEY PROTOCOL

APPENDIX 5. PRIVATE LANDS GUIDELINES

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LIST OF TABLES

TABLE 1. Designated primary core populations (13) by recovery unit................................................... xviii TABLE 2. Designated secondary core populations (10) by recovery unit. ................................................ xix TABLE 3. Designated essential support populations (16) by recovery unit................................................ xx TABLE 4. Species using normal and enlarged cavities excavated by red-cockaded woodpeckers TABLE 5. Number of active red-cockaded woodpecker clusters (2000) on private properties TABLE 6. Number of active red-cockaded woodpecker clusters (2000) on state properties TABLE 7. Number of active red-cockaded woodpecker clusters on federal and tribal properties in 1998, 1999, and 2000, by responsible agency TABLE 8. Primary core, secondary core, and essential support populations, and the properties that comprise these populations, by recovery unit TABLE 9. Significant and important support populations on state and federal properties, by recovery unit.

TABLE 10. Worksheet to assess population trend for all primary core, secondary core, and essential support populations, sorted by recovery unit TABLE 11. Recommended sample sizes for monitoring number of active clusters and potential breeding groups in red-cockaded woodpecker populations, by population size TABLE 12. Frequency of cavity suitability assessment by population size and trend TABLE 13. Rationale for foraging guidelines based on habitat structure (recovery standard) TABLE 14. Estimated time for each recovery population to meet size specified in delisting criteria, by recovery unit TABLE 15. Estimated minimum time for each recovery unit to meet downlisting criteria TABLE 16. Implementation schedule and estimated costs by recovery task TABLE 17. Estimated annual cost and schedule for implementation of recovery task 1.1.2 (maintain four suitable cavities in each active cluster) TABLE 18. Estimated annual cost for implementation of recovery task 1.2.3 (provision recruitment clusters equal to 10 percent of population, 4 artificial cavities each) TABLE 19. Estimated annual cost for implementation of recovery task 1.7 (burn entire area managed for red-cockaded woodpeckers at least once every 1 to 5 years) TABLE 20. Nestling characteristics indicative of nestling age, in number of days viii

LIST OF FIGURES

FIGURE 1. Relationships among fire, habitat components, arthropods, and fitness of red-cockaded woodpeckers as illustrated by a summary of research FIGURE 2. Diagrams of (a) adequate and (b) good foraging habitat FIGURE 3. Diagram of Copeyon-drilled cavity FIGURE 4. Diagram of Copeyon-drilled start FIGURE 5. Diagram of a cavity insert

Red-cockaded Woodpecker Recovery Plan Executive Summary ix

EXECUTIVE SUMMARY

CURRENT STATUS

The red-cockaded woodpecker (Picoides borealis) is a federally listed endangered species endemic to open, mature and old growth pine ecosystems in the southeastern United States. Currently, there are an estimated 14,068 red-cockaded woodpeckers living in 5,627 known active clusters across eleven states. This is less than 3 percent of estimated abundance at the time of European settlement. Red-cockaded woodpeckers were given federal protection with the passage of the Endangered Species Act in 1973.

Despite this protection, all monitored populations (with one exception) declined in size throughout the 1970’s and into the 1980’s. In the 1990’s, in response to intensive management based on a new understanding of population dynamics and new management tools, most populations were stabilized and many showed increases. Other populations remain in decline, and most have small population sizes. Our major challenge now is to bring about the widespread increases in population sizes necessary for recovery.

BASIC ECOLOGY AND POPULATION DYNAMICS

Red-cockaded woodpeckers are a cooperatively breeding species, living in family groups that typically consist of a breeding pair with or without one or two male helpers.

Females may become helpers, but do so at a much lower rate than males. The ecological basis of cooperative breeding in this species is unusually high variation in habitat quality, due to the presence or absence of a critical resource. This critical resource is the cavities that red-cockaded woodpeckers excavate in live pines, a task that commonly takes several years to complete.

Red-cockaded woodpeckers exploit the ability of live pines to produce large amounts of resin, by causing the cavity tree to exude resin through wounds, known as resin wells, that the birds keep open. This resin creates an effective barrier against climbing snakes. Longleaf pine is a preferred tree species for cavity excavation because it produces more resin, and for a longer period of time, than other southern pines.

Group living has profound influence over population dynamics. In non-cooperatively breeding birds, breeders that die are replaced primarily by the young of the previous year. Thus, variation in reproduction and mortality can have strong, immediate impacts on the size of the breeding population. However, in red-cockaded woodpeckers and other cooperative breeders, a large pool of helpers is available to replace breeders.

As a result, the size of the breeding population is not strongly affected by how many young are produced each year, or even on how many breeders may die. Because of this, we use the number of potential breeding groups rather than number of individuals as our measure of population size. A potential breeding group is an adult female and adult male that occupy the same cluster, with or without one or more helpers, whether or not they attempt to nest or successfully fledge young.

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Because of the cooperative breeding system, red-cockaded woodpecker populations are unusually resistant to environmental and demographic variation, but highly sensitive to the spatial arrangement of habitat. The buffering effect of helpers against annual variation operates only when helpers can readily occupy breeding vacancies as they arise. Helpers do not disperse very far and typically occupy vacancies on their natal territory or a neighboring one. If groups are isolated in space, dispersal of helpers to neighboring territories is disrupted and the buffering effect of the helper class is lost. When this happens, populations become much less likely to persist through time.

Also, the cooperative breeding system does not allow rapid natural growth of populations. Colonization of unoccupied habitat is an exceedingly slow process under natural conditions, because cavities take long periods of time to excavate and birds do not occupy habitat without cavities. As forests age and old pines become abundant, rates of natural cavity excavation and colonization may increase.

Understanding these three components of the population dynamics of red-cockaded woodpeckers provides us the foundation for recovery efforts: (1) population size and trend are determined by the number of potential breeding groups rather than annual variation in reproduction and survival; (2) the buffering capacity of the helper class must be maintained, by maintaining close aggregations of territories; and (3) colonization of unoccupied habitat will be very slow without management assistance.

HABITAT REQUIREMENTS AND LIMITING FACTORS

Red-cockaded woodpeckers require open pine woodlands and savannahs with large old pines for nesting and roosting habitat (clusters). Large old pines are required as cavity trees because the cavities are excavated completely within inactive heartwood, so that the cavity interior remains free from resin that can entrap the birds. Also, old pines are preferred as cavity trees, because of the higher incidence of the heartwood decay that greatly facilitates cavity excavation. Cavity trees must be in open stands with little or no hardwood midstory and few or no overstory hardwoods. Hardwood encroachment resulting from fire suppression is a well-known cause of cluster abandonment. Red-cockaded woodpeckers also require abundant foraging habitat. Suitable foraging habitat consists of mature pines with an open canopy, low densities of small pines, little or no hardwood or pine midstory, few or no overstory hardwoods, and abundant native bunchgrass and forb groundcovers.

Limiting factors are those that directly affect the number of potential breeding groups, because this is the primary determinant of population size and trend. Several factors currently impact the persistence of breeding groups. Foremost among these are the factors that limit suitable nesting habitat, namely fire suppression and lack of cavity trees. Fire suppression has resulted in loss of potential breeding groups throughout the range of red-cockaded woodpeckers, because the birds cannot tolerate the hardwood encroachment that results from lack of fire. This limitation is addressed through the use of prescribed burning. Lack of cavity trees, and potential cavity trees, limits the number of breeding groups in most populations. This limitation is addressed in the short-term xi through cavity management tools such as artificial cavities and restrictor plates, and over the long-term by growing large old trees in abundance.

Another factor directly limiting the number of potential breeding groups is habitat fragmentation and consequent isolation of groups, which results in disrupted dispersal of helpers and failure to replace breeders. This limitation is best addressed through the appropriate placement of clusters of artificial cavities, and implementation of silvicultural practices that minimize fragmentation.

There are several other threats to the existence and recovery of the species, not limiting most populations currently, but which will become more important as the current limitations are addressed. Chief among these are (1) degradation of foraging habitat through fire suppression and loss of mature trees, and (2) loss of valuable genetic resources because of small size and isolation of populations. As currently limiting factors such as lack of cavities are relieved, the continued growth and natural stability of red-cockaded woodpecker populations will depend on provision of abundant, good quality foraging habitat and careful conservation of genetic resources.

POPULATION AND SPECIES VIABILITY

Four types of threats to species and population viability have been identified:

genetic stochasticity (consisting of both inbreeding and genetic drift), demographic stochasticity, environmental stochasticity, and catastrophes. We now have some knowledge of population sizes of red-cockaded woodpeckers necessary to withstand these extinction threats, primarily from research performed with a spatially explicit, individually based simulation model of population dynamics developed specifically for this species.

Red-cockaded woodpeckers exhibit inbreeding depression and inbreeding avoidance behaviors. Inbreeding is expected to affect population viability in populations of less than 40 potential breeding groups, and may be a significant factor affecting viability in isolated populations of 40 to 100 potential breeding groups as well.

Immigration rates of 2 or more migrants per year can effectively reduce inbreeding in populations of any size, including very small ones.

Effects of demographic stochasticity on population viability vary with the spatial arrangement of groups. Populations as small as 25 potential breeding groups can be surprisingly resistant to random demographic events, if those groups are highly aggregated in space. Populations as large as 100 potential breeding groups can be impacted by demographic stochasticity, if groups are not aggregated and dispersal of helpers is disrupted. Demographic stochasticity is not expected to affect populations larger than 100 potential breeding groups. Similarly, effects of environmental stochasticity vary with the spatial arrangement of groups. Based on preliminary results of the model and estimates of environmental stochasticity derived from the North Carolina xii

Sandhills, 250 potential breeding groups will likely withstand effects of environmental stochasticity regardless of their spatial arrangement.

Loss of genetic variation through the process of genetic drift is an inevitable consequence of finite population size. New genetic variation arises through the process of mutation. In large populations, mutation can offset loss through drift and genetic variation is maintained. Just how large a population must be to maintain variation is a difficult question. Currently, researchers recognize that in general, only populations with actual sizes in the thousands, rather than hundreds, can maintain long-term viability and evolutionary potential in the absence of immigration. However, if populations are connected by immigration rates on the order of 1 to 10 migrants per generation (0.5 to 2.5 migrants per year), the genetic variation maintained by these populations is equal to that of one population as large as the sum of the connected populations. Thus, sufficient connectivity among populations can maintain genetic variation and long-term viability for the species.

RECOVERY GOAL

The ultimate recovery goal is species viability. This goal is represented by delisting. Once delisting criteria are met, the size, number, and distribution of populations will be sufficient to counteract threats of demographic, environmental, genetic, and catastrophic stochastic events, thereby maintaining long-term viability for the species as defined by current understanding of these processes. Regions and habitat types currently occupied by the species will be represented to the best of our ability, given habitat limitations.

RECOVERY CRITERIA

Recovery criteria have been formulated using eleven recovery units delineated according to ecoregions. Populations required for recovery are distributed among recovery units to ensure the representation of broad geographic and genetic variation in the species. Viable populations within each recovery unit, to the extent allowed by habitat limitations, are essential to the recovery of the species as a whole.

Population sizes identified in recovery criteria are measured in number of potential breeding groups. A potential breeding group is an adult female and adult male that occupy the same cluster, with or without one or more helpers, whether or not they attempt to nest or successfully fledge young. A traditional measure of population size has been number of active clusters. Potential breeding groups is used in recovery criteria in addition to active clusters, because number of active clusters can include varying proportions of solitary males and captured clusters. (A captured cluster is one that does not support its own group, but is kept active by a member or members of a neighboring group.) Increases in proportions of captured clusters and solitary males are early indicators of population decline. Estimates of all three parameters—number of active xiii clusters, proportion of solitary males, and proportion of captured clusters—are required to derive estimates of potential breeding groups.

To facilitate use of potential breeding groups as a measure of population size, we have provided a range of numbers of active clusters considered the likely equivalents of the required number of potential breeding groups. Estimated number of active clusters is likely to be at least 1.1 times the number of potential breeding groups, but it is unlikely to be more than 1.4 times this number. Thus, an estimated 400 to 500 active clusters will be necessary to contain 350 potential breeding groups, depending on the proportions of solitary males and captured clusters and also on the estimated error of the sampling scheme. It is expected that all recovery populations will have sampling in place that is adequate to judge potential breeding groups. If this is not the case, only the highest number of active clusters in the range given can be substituted to meet the required population size.

Delisting

Delisting shall occur when each of the following criteria is met. Rationale for each criterion is given immediately following this list. See Tables 1, 2, and 3 for population designation. All properties identified as part or all of a recovery population (Tables 1, 2, and 3) should be managed for maximum size that the habitat designated for red-cockaded woodpeckers will allow. (Maximum size is generally based on 200 ac [81 ha] per group).

Criterion 1. There are 10 populations of red-cockaded woodpeckers that each contain at least 350 potential breeding groups (400 to 500 active clusters), and 1 population that contains at least 1000 potential breeding groups (1100 to 1400 active clusters), from among 13 designated primary core populations, and each of these 11 populations is not dependent on continuing installation of artificial cavities to remain at or above this population size. The 13 designated primary core populations, and the recovery units in which they are located, are listed in Table 1.

Criterion 2. There are 9 populations of red-cockaded woodpeckers that each contain at least 250 potential breeding groups (275 to 350 active clusters), from among 10 designated secondary core populations, and each of these 9 populations is not dependent on continuing installation of artificial cavities to remain at or above this population size.

The 10 designated secondary core populations, and the recovery units in which they are located, are listed in Table 2.

Criterion 3. There are at least 250 potential breeding groups (275 to 350 active clusters) distributed among designated essential support populations in the South/Central Florida Recovery Unit, and six of these populations (including at least two of the following:

Avon Park, Big Cypress, and Ocala) exhibit a minimum population size of 40 potential breeding groups that is independent of continuing artificial cavity installation.

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Designated essential support populations in the South/Central Florida Recovery Unit are listed in Table 3.

Criterion 4. The following populations are stable or increasing and each contain at least 100 potential breeding groups (110 to 140 active clusters): (1) Northeast North Carolina/Southeast Virginia Essential Support Population of the Mid-Atlantic Coastal Plain Recovery Unit, (2) Talladega/Shoal Creek Essential Support Population of the Cumberlands/Ridge and Valley Recovery Unit, and (3) North Carolina Sandhills West Essential Support Population of the Sandhills Recovery Unit; and these populations are not dependent on continuing artificial cavity installation to remain at or above this population size. These populations are also listed in Table 3.

Criterion 5. For each of the populations meeting the above size criteria, responsible management agencies shall provide (1) a habitat management plan that is adequate to sustain the population and emphasizes frequent prescribed burning, and (2) a plan for continued population monitoring.

Rationale for Delisting Criteria

Criterion 1. A population size of 350 potential breeding groups is considered highly robust to threats from environmental stochasticity as well as inbreeding and demographic stochasticity. It is the lowest current estimate of the minimum size necessary to offset losses of genetic variation through genetic drift. One primary core population has the potential to harbor 1000 potential breeding groups within the near future; this criterion is included because such a large population may well be resistant to loss of genetic variation through drift. Eleven of 13 primary core populations are required for delisting because it is recognized that at any given time, one or two may be suffering hurricane impacts.

Thirteen primary core populations are designated because of available habitat and because this number, together with 10 secondary core populations (below), may serve to facilitate natural dispersal among populations and maximize retention of genetic variability. Primary and secondary core populations provide for the conservation of the species within each major physiographic unit in which it currently exists, with the exception of South/Central Florida. This recovery unit is represented by several, smaller, essential support populations (below). Populations that depend on continuing artificial cavity installation to maintain stable or increasing trends are barred from meeting delisting criteria because this management technique is considered appropriate for short-term management only.

Criterion 2. A population size of 250 potential breeding groups is the minimum size considered robust to environmental stochasticity, and is well above the size necessary to withstand inbreeding and demographic stochasticity. Nine of 10 designated secondary core populations are required for delisting to allow for hurricane impacts.

Criterion 3. This unique habitat type is represented to the extent that available habitat allows. Unique genetic resources are conserved as much as reasonably possible.

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Because of small size, some of these populations will remain vulnerable to extinction threats and may eventually be lost. The likelihood of extirpation of small populations is minimized by enhancing the spatial arrangement of territories so that they are highly aggregated.

Criterion 4. These unique or important habitats, and genetic resources contained within this population, will be represented at the time of delisting. This population size is midway in estimates of sizes necessary to withstand threats from inbreeding depression and is considered robust to demographic stochasticity if territories are moderately aggregated in space.

Criterion 5. Continued habitat management and population monitoring are necessary to ensure that the species does not again fall to threatened or endangered status.

Downlisting

Downlisting shall occur when each of the following criteria is met. Rationale for each criterion is presented immediately following this list.

Criterion 1. The Central Florida Panhandle Primary Core Population in the East Gulf Coastal Plain Recovery Unit is stable or increasing and contains at least 350 potential breeding groups (400 to 500 active clusters).

Criterion 2. There is at least one stable or increasing population containing at least 250 potential breeding groups (275 to 350 active clusters) in each of the following recovery units: Sandhills, Mid-Atlantic Coastal Plain, South Atlantic Coastal Plain, West Gulf Coastal Plain, Upper West Gulf Coastal Plain, and Upper East Gulf Coastal Plain.

Criterion 3. There is at least one stable or increasing population containing at least 100 potential breeding groups (110 to 140 active clusters) in each of the following recovery units: Mid-Atlantic Coastal Plain, Sandhills, South Atlantic Coastal Plain, and East Gulf Coastal Plain.

Criterion 4. There is at least one stable or increasing population containing at least 70 potential breeding groups (75 to 100 active clusters) in each of four recovery units, Cumberlands/Ridge and Valley, Ouachita Mountains, Piedmont, and Sandhills. In addition, the Northeast North Carolina/Southeast Virginia Essential Support Population is stable or increasing and contains at least 70 potential breeding groups (75 to 100 active clusters).

Criterion 5. There are at least four populations each containing at least 40 potential breeding groups (45 to 60 active clusters) on state and/or federal lands in the South/Central Florida Recovery Unit.

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Criterion 6. There are habitat management plans in place in each of the above populations identifying management actions sufficient to increase the populations to recovery levels, with special emphasis on frequent prescribed burning during the growing season.

Rationale for Downlisting Criteria

Criterion 1. A population size of 350 potential breeding groups is considered highly robust to threats from environmental stochasticity as well as inbreeding and demographic stochasticity. It is the lowest current estimate of the minimum size necessary to offset losses of genetic variation through genetic drift.

Criterion 2. This population size, 250 potential breeding groups, is sufficient to withstand extinction threats from environmental uncertainty, demographic uncertainty, and inbreeding depression. These 6 populations, in combination with the single population identified in criterion (1), will represent each major recovery unit.

Criterion 3. A second population in these coastal recovery units will decrease the species’ vulnerability to hurricanes. The West Gulf Coastal Plain is excluded because there are no candidate populations there. The lower size, 100 potential breeding groups, is considered sufficient to withstand threats from demographic uncertainty and inbreeding depression, and is much more quickly attained than 250 potential breeding groups thought necessary to withstand environmental stochasticity.

Criterion 4. These special habitats will be represented at the time of downlisting. This population size is midway in estimates of sizes necessary to withstand threats from inbreeding depression and is considered robust to demographic stochasticity if territories are moderately aggregated in space.

Criterion 5. This unique region will be represented at the time of downlisting. Forty potential breeding groups is at the lower end of estimates of sizes necessary to withstand inbreeding depression and are considered robust to demographic stochasticity if territories are highly aggregated in space.

Criterion 6. These habitat management plans are necessary to ensure progress toward delisting.

ACTIONS NEEDED

The primary actions needed to accomplish the ultimate (delisting) and interim (downlisting) recovery goals are (1) application of frequent fire to both clusters and foraging habitat, (2) protection and development of large, mature pines throughout the landscape, (3) protection of existing cavities and judicious provisioning of artificial cavities, (4) provision of sufficient recruitment clusters in locations chosen to enhance the xvii spatial arrangement of groups, and (5) restoration of sufficient habitat quality and quantity to support the large populations necessary for recovery.

DATE OF RECOVERY

We estimate that, with full implementation of this recovery plan, red-cockaded woodpeckers will be downlisted by the year 2050 and delisted by 2075.

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TABLE 1. Designated primary core populations (13) by recovery unit. Location (state) and individual properties comprising recovery populations are also listed. At delisting, the Central Florida Panhandle will contain 1000 or more potential breeding groups, and at least 11 of the remaining 12 primary core populations will contain 350 or more potential breeding groups. See 7 for more information, including definitions of recovery roles and recovery units. See map insert also.

Recovery Unit Population

Property Full Name

State

East Gulf Coastal Plain

(1) Central Florida Panhandle Apalachicola Ranger District, Apalachicola National Forest FL Ochlockonee River State Park FL St. Marks National Wildlife Refuge FL Tate's Hell State Forest FL Wakulla Ranger District, Apalachicola National Forest FL

(2) Chickasawhay Chickasawhay Ranger District, DeSoto National Forest MS

(3) Eglin Eglin Air Force Base FL

Mid-Atlantic Coastal Plain

(4) Coastal North Carolina Croatan National Forest NC Holly Shelter Game Lands NC Marine Corps Base Camp Lejeune NC

(5) Francis Marion Francis Marion National Forest SC

Sandhills

(6) Fort Benning Fort Benning GA

(7) North Carolina Sandhills East Calloway Tract NC Carver's Creek Tract NC Fort Bragg NC McCain Tract NC Weymouth Woods State Nature Preserve NC

South Atlantic Coastal Plain

(8) Fort Stewart Fort Stewart GA

(9) Osceola/Okefenokee Osceola National Forest FL Okefenokee National Wildlife Refuge GA

Upper East Gulf Coastal Plain

(10) Bienville Bienville National Forest MS

Upper West Gulf Coastal Plain

(11) Sam Houston Sam Houston National Forest TX

West Gulf Coastal Plain

(12) Angelina/Sabine Angelina National Forest TX Sabine National Forest TX

(13) Vernon/Fort Polk Fort Polk LA Vernon Unit, Calcasieu Ranger District, Kisatchie National LA Forest xix

TABLE 2. Designated secondary core populations (10) by recovery unit. Location (state) and individual properties comprising recovery populations are also listed. At delisting, at least 9 of these populations will contain 250 or more potential breeding groups. See 7 for more information, including definitions of recovery roles and recovery units. See map insert also.

East Gulf Coastal Plain

(1) Conecuh/Blackwater Blackwater River State Forest FL Conecuh National Forest FL

(2) DeSoto DeSoto Ranger District, DeSoto National Forest MS

(3) Homochitto Homochitto National Forest MS

Ouachita Mountains

(4) Ouachita Ouachita National Forest AR

Piedmont

(5) Oconee/Piedmont Oconee National Forest GA Piedmont National Wildlife Refuge GA

Sandhills

(6) South Carolina Sandhills Carolina Sandhills National Wildlife Refuge SC Sand Hills State Forest SC

South Atlantic Coastal Plain

(7) Savannah River Savannah River Site SC

Upper East Gulf Coastal Plain

(8) Oakmulgee Oakmulgee Ranger District, Talladega National Forest AL

West Gulf Coastal Plain

(9) Catahoula Catahoula Ranger District, Kisatchie National Forest LA Winn Ranger District (portion), Kisatchie National Forest LA

(10) Davy Crockett Davy Crockett National Forest TX xx

TABLE 3. Designated essential support populations (16) by recovery unit. Location (state) and individual properties comprising recovery populations are also listed. At delisting, North Carolina Sandhills West, Northeast North Carolina/Southeast Virginia, and Talladega/Shoal Creek will each contain 100 or more potential breeding groups, and 6 populations (including at least 2 of the following: Avon Park, Big Cypress, and Ocala) in South/Central Florida will each contain 40 or more potential breeding groups. See 7 for more information, including definitions of recovery roles and recovery units. See map insert also.

Cumberlands/Ridge and Valley

(1) Talladega/Shoal Creek Shoal Creek Ranger District, Talladega National Forest AL Talladega Ranger District, Talladega National Forest AL

Mid-Atlantic Coastal Plain

(2) Northeast North Carolina/

Southeast Virginia Alligator River National Wildlife Refuge NC Dare County Bombing Range NC Palmetto-Peartree Preserve NC Pocosin Lakes National Wildlife Refuge NC Piney Grove Preserve VA

Sandhills

(3) North Carolina Sandhills West Camp Mackall NC Sandhills Game Lands NC

South/Central Florida

(4) Avon Park Avon Park Air Force Range FL Kicco Wildlife Management Area FL

(5) Babcock/Webb Babcock/Webb Wildlife Management Area FL

(6) Big Cypress Big Cypress National Preserve FL

(7) Camp Blanding Camp Blanding Training Site FL

(8) Corbett/Dupuis J. W. Corbett/Dupuis Wildlife Management Area FL

(9) Goethe Goethe State Forest FL

(10) Hal Scott Preserve Hal Scott Preserve FL

(11) Ocala Ocala National Forest FL

(12) Picayune Strand Picayune Strand State Forest FL

(13) St. Sebastian River St. Sebastian River State Buffer Preserve FL

(14) Three Lakes Three Lakes Wildlife Management Area FL

(15) Withlacoochee – Citrus Tract Withlacoochee State Forest - Citrus Tract FL

(16) Withlacoochee – Croom Tract Withlacoochee State Forest - Croom Tract FL

Red-cockaded Woodpecker Recovery Plan 1A. Reasons for Listing

PART I. INTRODUCTION

1. LISTING

A. REASONS FOR LISTING

The red-cockaded woodpecker was listed as endangered in 1970 (35 Federal Register 16047) and received federal protection with the passage of the Endangered Species Act in 1973. Once a common bird distributed continuously across the southeastern United States, by the time of listing the species had declined to fewer than 10,000 individuals in widely scattered, isolated, and declining populations (Jackson 1971, Ligon et al. 1986).

This precipitous decline was caused by an almost complete loss of habitat. Fire-maintained old growth pine savannahs and woodlands that once dominated the southeast, on which the woodpeckers depend, no longer exist except in a few small patches.

Longleaf pine (Pinus palustris) ecosystems, of primary importance to red-cockaded woodpeckers, are now among the most endangered systems on earth (Simberloff 1993, Ware et al. 1993). Shortleaf (P. echinata), loblolly (P. taeda), and slash pine (P. elliottii) ecosystems, important to red-cockaded woodpeckers outside the range of longleaf, also have suffered severe declines (Smith and Martin 1995).

Loss of the original pine ecosystems was primarily due to intense logging for lumber and agriculture. Logging was especially intense at the turn of the century (Frost 1993, Martin and Boyce 1993, Conner et al. 2001). Two additional factors resulting in the loss of original pine systems in the 1800’s and earlier were exploitation for pine resins and grazing by free-ranging hogs (Sus scrofa; Wahlenburg 1946, Frost 1993).

Later, in the 1900’s, fire suppression and detrimental silvicultural practices had major impacts on primary ecosystem remnants, second-growth forests, and consequently on the status of red-cockaded woodpeckers (Frost 1993, Ware et al. 1993, Ligon et al. 1986, 1991, Landers et al. 1995, Conner et al. 2001). Longleaf pine suffered a widespread failure to reproduce following initial cutting, at first because of hogs and later because of fire suppression (Wahlenburg 1946, Ware et al. 1993). These factors are discussed in more detail below.

Loss of the Original Ecosystems

Southern pine savannahs and open woodlands once dominated the southeastern United States, and may have totaled over 80 million ha (200 million ac) at the time of European colonization (Conner et al. 2001). Longleaf pine communities characterized the Atlantic and Gulf coastal regions, and covered an estimated 24 to 37 million ha (60 to 92 million ac; Wahlenburg 1946, Frost 1993, Ware et al. 1993, Landers et al. 1995).

Roughly one quarter of the longleaf communities also supported other pines such as loblolly, shortleaf, slash, and pond pine (P. serotina) in various proportions depending on soil conditions, especially in transitional zones between the coastal plains and other physiographic regions (Frost 1993, Landers et al. 1995).

Today, longleaf forests have declined to less than 1.2 million ha (3 million ac;

Landers et al. 1995), of which roughly 3 percent remains in relatively natural condition (Frost 1993). Little old growth remains, and virtually no longleaf forest has escaped changes in the natural fire regime (Simberloff 1993, Walker 1999). Shortleaf pine was prevalent outside the range of longleaf, especially on dry slopes and ridges in the Interior Highlands and Oklahoma, and has declined considerably (Landers 1991, Smith and Martin 1995). In the precolonial forests, loblolly pine was present as a minor component of riparian hardwood ecosystems or in association with shortleaf pine in some upland interior forests (White 1984, Landers 1991, Christensen 2000).

Southern pine forests today are very different from precolonial communities not only in extent, but also in species composition, age, and structure (Ware et al. 1993, Noel et al. 1998). Original pine forests were old, open, and contained a structure of two layers:

canopy and diverse herbaceous groundcover. These forests were dominated by longleaf pine in the coastal plain, longleaf and shortleaf pines in the Piedmont and interior highlands, and slash pine (P. elliottii var. densa) in south Florida. Forests dominated by loblolly pine were restricted to a portion of southern Arkansas and perhaps eastern Virginia and extreme northeastern North Carolina (White 1984, Christensen 2000). In contrast, much of today’s forest is young, dense, and dominated by loblolly pine, with a substantial hardwood component and little or no herbaceous groundcover (Ware et al.

1993, Noel et al. 1998).

Original longleaf communities in the Atlantic and Gulf coastal plains were first heavily impacted by exploitation for naval stores and then virtually eliminated by widespread logging and the subsequent reproductive failure of longleaf pine (Frost 1993, Ware et al. 1993). Naval stores industries harvested pine resin for the production of tar, pitch, and turpentine—commodities in high demand during colonial times. Pine woodlands were logged for lumber and conversion to agricultural fields. Impacts to easily accessible areas began with the arrival of Europeans, but technological developments of the 1800’s, such as the copper still, steam power, and especially railroads, dramatically increased the rate and area of loss (Frost 1993). In the late 1800’s logging operations moved to the previously inaccessible interior forests of longleaf, shortleaf, and loblolly pines. For over a decade these operations removed a reported 3 to 4 billion board feet per year (Frost 1993); an estimated 13 billion board feet of longleaf was extracted in 1907 alone (Wahlenburg 1946, Landers et al. 1995). This especially intense period of logging from 1870 to 1930 resulted in the loss of nearly all of the remaining old growth forest in the southeast (Frost 1993, Martin and Boyce 1993, Conner et al. 2001).

A common logging practice before the late 1800’s was to leave a fair number of residual trees, including small trees, some of those infected with red heart fungus (Phellinus pini), and some that had been boxed for resin production (Wahlenburg 1946, Conner et al. 2001). Cavity trees of red-cockaded woodpeckers probably were left in much higher proportion than their numbers, due to the likelihood of red heart infection and the abundant resin coating. These residual pines enabled the red-cockaded woodpeckers to survive the original devastation (Phillips and Hall 2000). Loss of residual trees in the twentieth century has been a major factor in the decline of woodpecker populations (Costa and Escano 1989, Conner et al. 2001; see 2D).

Fire Suppression

Precolonial fire frequencies in the southeast have been estimated at 1 to 3 years for the Atlantic and lower Gulf coastal plains (Stout and Marion 1993, Ware et al. 1993, Frost 1998), 4 to 6 years for the Piedmont and upper Gulf coastal plain, and 7 to 25 years for the southern Appalachians and interior highlands (Masters et al. 1995, Frost 1998).

Fire frequency increases with size of fire compartments, and natural firebreaks in the southeastern coastal plains were rare (Ware et al. 1993, Frost 1998). Historically, fires were ignited by Native Americans and by lightning. Lightning was the primary ignition source shaping the evolution of these fire-maintained ecosystems, but Native Americans may have played a substantial role in maintaining them (Delcourt et al. 1993, Frost 1993). Such maintenance vanished, of course, as Native Americans were severely impacted by the diseases and aggression of incoming Europeans. Natural fire frequency also declined as fires were reduced in area because of roads, plowed fields, and other human-made firebreaks (Frost 1993, Ware et al. 1993).

Europeans brought their perceptions of fire with them as they colonized North

America. In Europe, fire was an integral part of traditional swidden agriculture (i.e., shifting cultivation) and was celebrated by peasants as a source of renewal (Pyne 1998).

In contrast, urban intellectuals and authorities viewed fire as a destructive force. This view was rooted in a social context: controlling the use of fire could facilitate control of the populace by discouraging the nomadic system (Pyne 1998).