Biological Evaluation Regional Forester's Sensitive Species

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Biological Evaluation Regional Forester’s Sensitive Species Shawnee Vegetation Management Strategy Shawnee National Forest INTRODUCTION Forest Service Manual (FSM) Section 2672.41 requires a biological evaluation (BE) and/or biological assessment (BA) be conducted for all Forest Service planned, funded, executed, or permitted programs and activities. The objectives of this BE are: 1) to ensure that Forest Service actions do not contribute to the loss of population viability of any native or desired non-native species or contribute to trends toward federal listing; 2) to comply with the requirements of the Endangered Species Act (ESA) so that federal agencies do not jeopardize or adversely modify critical habitat (as defined in ESA) of any federally listed species; and, 3) to provide a process and standard ensuring that federally threatened or endangered and Regional Forester’s Sensitive plants receive full consideration in the decision-making process.

The Shawnee National Forest has known occurrences of federally threatened or endangered and Regional Forester’s Sensitive (TES) plant species, which were considered in this analysis. This BE provides documentation of the analysis of potential effects of the proposed action to TES plant species and associated habitats. It also serves as biological input for the environmental analysis of project-level decision making to ensure compliance with the ESA National Environmental Policy Act (NEPA) and National Forest Management Act (NFMA).

PURPOSE AND NEED FOR PROPOSED ACTION Location of the Proposed Project Area The Shawnee Vegetation Management Strategy project area encompasses all 286,000 acres of the Shawnee National Forest, located in the southernmost 11 counties of Illinois. About 280,000 National Forest System acres are forested (73 percent oak-hickory, 17 percent pine, and 10 percent in other hardwood forest types). The Shawnee National Forest (Forest) contains 80 natural areas, designated to preserve their special features. In many cases, the special features are unique plant communities. Maintaining the oak-hickory forest community in general, in particular natural area plant communities, is a focus of the 2006 Land and Resource Management Plan (Forest Plan) (USDA FS 2006). Existing Conditions Oak forest types dominate the landscape of the Shawnee, making up nearly 73% of its total forested acres. Oak types include forests where oaks consist of over half of the composition. The next closest forest type is pine at 17%, with the remaining 10% falling under other hardwood types.

However, the forest is aging. Currently, nearly 75% of all forest stands are over 70 years of age. This is important because many oak species (particularly red and black oak) do not live much past 120 years. Because fire on the landscape has been drastically reduced, much of the native oak-hickory forest is being replaced by tree species much more tolerant of the increasingly shady conditions of the forest floor. Maple, beech, ash and tulip poplar are replacing oak in the understory—a process called mesophication. Without intervention, these shade-tolerant trees will become the dominant forest type across much of the Forest. In addition, many of the rare, open-canopy habitat types in natural areas are becoming degraded because of woody succession, as eastern redcedar, sassafras, and other species increasingly dominate the sites.

The spread non-native invasive plants is also altering forests and natural communities across the Forest. Several past decisions have authorized integrated pest management of invasive plant infestations for many species in several specified sites. A broad array of treatments, including the use of herbicides, have been implemented. However, only a small portion of non-native invasive plant infestations have been treated. New sites and new species are continually being reported by Forest personnel, contractors, and members of the public. Most of those have not yet been authorized for treatment. As a result, many infestations have rapidly expanded and spread. In other words, it has been difficult to implement EDRR for control non-native invasive plants. The proliferation of those species is reducing plant diversity in natural areas, wildernesses, and in forests on the Shawnee National Forest.

Woody encroachment of native, shade tolerant species also threatens habitat for many RFSS plants. Although species that grow in open, sunny habitat such as glades, barrens, prairies, and cliffs are particularly vulnerable, RFSS plants growing in many other habitat types are threatened by forest succession and other types of woody encroachment. Populations of many other RFSS plants are vulnerable to this threat. These plants grow in variety of habitats, such as acid seep springs, wetlands, streams, and various types of woodlands, ranging from very dry to wet.

Decades of fire suppression has accelerated forest succession across the Forest. While the recent expansion of prescribed fire has had encouraging results, with forest succession slowed or even reversed at several sites, some shade tolerant woody species have been difficult to suppress with fire alone. Stand improvement cutting maple, ash, and beech has also been implemented. However, these species have often re-sprouted vigorously when they were not also treated with herbicides. Purpose The USDA Forest Service is proposing to implement management activities on the Shawnee National Forest as part of the Shawnee Vegetation Management Strategy. The project is designed to achieve multiple-resource benefits and work towards Desired Future Conditions described in the 2006 Shawnee National Forest Land and Resource Management Plan. Since the forest plan is a guiding document for forest management and is summarized and quoted throughout this assessment, we tier the environmental assessment to the forest plan and its supporting analysis (40 CFR 1502.20). The proposal in this project includes the use of non-commercial stand improvement activities and the application of herbicides.

The purpose of this project is to maintain or restore the desired oak-hickory forests and other natural communities on the Forest by addressing two major threats: 1) nonnative invasive plant infestations and 2) undesirable, shade-tolerant or other encroaching, native vegetation. Plant and animal habitats of the Shawnee National Forest are imperiled because of the adverse effects of non-native invasive plant infestations and the encroachment and proliferation of undesirable woody plants. Adverse effects

2 caused by these two threats include loss of biological diversity; loss of natural wildlife habitat, including habitat used by threatened, endangered, and sensitive species; loss of structural diversity important for specific wildlife niches; changes in water regimes, fire regimes, or both; changes in soil nutrient cycling and microbial populations; decreased quality of recreational experiences; and forests that are less diverse, less healthy and subsequently less resilient.

This project is needed to accomplish the resource goals of the Shawnee National Forest as established in the forest plan:

• There is a need to maintain and restore biological diversity by reducing, controlling, and eradicating nonnative invasive species. o This need is addressed in forest plan goals B-Ecosystem Management, G-Special Feature Management, K-Forest Ecosystem Health and Sustainability, and M-Wildlife, Fish and At- Risk Species Management (USDA Forest Service 2006, pages 5, 12, 13, 15, 16, 21, 22, 23, 42, 43, 46, 47, 59, and 76). • There is a need to maintain and restore the oak-hickory ecosystem resilience by reducing shade- tolerant understory competition, creating light conditions favorable for the establishment of oak-hickory regeneration; improving forest structure through the maintenance of early successional habitat; reducing stressors caused by overstocked conditions; and improving and enhancing the health, vigor, and growth of existing trees and native vegetation communities. o This need is addressed in forest plan goals B-Ecosystem Management, K-Forest Ecosystem Health and Sustainability, and M-Wildlife, Fish and At-Risk Species Management (USDA Forest Service 2006, pages 5, 12, 13, 15, 16, 19, 21, 22, 23, 42, 43, 59, 60, 154, and 297). • There is a need to preserve and maintain remnants of rare plant communities. Unique natural environments (e.g. savannas, barrens, prairies, glades) need to be protected, restored and maintained through active management programs. o This need is addressed in forest plan goals B-Ecosystem Management, G-Special Feature Management, K-Forest Ecosystem Health and Sustainability, and M-Wildlife, Fish and At- Risk Species Management (USDA Forest Service 2006, pages 5, 12, 13, 15, 16, 21, 22, 23, 42, 43, 46, 47, 59, and 76). PROPOSED ACTION AND ALTERNATIVES Alternative 1—No Action Under this alternative, current management (based on past decisions) would continue. None of the proposed management activities would be implemented. Alternative 2—Proposed Action The proposed action is an integrated management strategy to maintain and restore a biologically diverse oak-hickory ecosystem using several herbicides. The herbicides will be used in conjunction with other treatments, such as forest stand improvement or small tree and brush removal, to create a forest- wide, integrated vegetation management strategy focused on two objectives:

1. Stand improvements to suppress undesirable shade-tolerant or other encroaching vegetation.

a. Manual chainsaw, brush-saw, ax, and hand saw use to cut woody vegetation up to 9 inches in diameter followed by stump application of herbicides to prevent sprouting b. Girdling, stem injection, or hack and squirt of encroaching vegetation of any size c. Foliar herbicide application using a hand-held applicator or backpack sprayer 2. Treatment of non-native invasive plants with priority given to early detection of, and rapid response to, new invaders. The goal is prevention, eradication, suppression, and reduction of existing and future nonnative invasive plant infestations. a. Chemical treatment using herbicides that target identified non-native invasive plants using a hand-held applicator, backpack sprayer, or boom-mounted spray rig. b. Manual and mechanical techniques, such as cutting, pulling, mowing, or girdling of non- native invasive plants.

Other important components of the proposed action are the following: • Before treatment would occur, a site-specific interdisciplinary review would address any potential impacts to cultural resources, karst, threatened, endangered, or sensitive plants or animals, and other applicable resource areas. This review would be conducted using the Pretreatment Checklist Required for all NNIS Treatment Areas (Shawnee Vegetation Management Strategy EA, Appendix B). The Forest would choose a different method of treatment if staff anticipates adverse effects from use of any treatment method (chemical, manual, or mechanical). • No aerial or large-scale broadcast spraying of herbicides will be permitted under this project. • No treatments of ponds, lakes, or flowing streams will be permitted under this project. • All herbicides will be applied strictly in accordance with the label directions and we would adhere to all state and federal pesticide laws. • Herbicides will be applied under the direction of a licensed applicator. • Most non-native invasive plant sites would require follow-up treatments in future years. • Forest-wide Standards and Guidelines and Project Design Criteria (Shawnee Vegetation Management EA, Tables 6-A through 6-G) will be followed. • In order to limit the potential effects of the proposed action, herbicide treatments, including treatments authorized by previous decisions, will be limited to 3,270 acres per year – 1.1% of the forest to include: o Up to 1,270 acres of forest stand improvement treatments per year – 0.4% of the forest. The Forest Plan envisions 1.270 yearly stand improvement acres in the second decade of the Forest Plan across the Forest. o Up to 2,000 acres of non-native invasive plant treatments – 0.7% of the forest. Previous decisions allow the treatment of nearly 2,000 acres per year. The intent of the Shawnee Vegetation Management is not to increase the total treated acres per year, but to provide flexibility on treatment options.

This forest-wide integrated vegetation management strategy considers the best available scientific information, current and future nonnative invasive plant inventories, and effectiveness of treatments designed to meet desired objectives to control both non-native invasive plant infestations and shade- tolerant encroachment on the Forest. Treatments would be employed alone, in combination, or with other current or future vegetation management projects to achieve the most effective results.

Table 1. Comment herbicide controls Examples of Examples of plants to be Chemical Name Targeted Use Risk Assessment Trade Names targeted Milestone® Broadleaf selective: foliar Kudzu, autumn olive, tree Aminopyralid Durkin 2007 Milestone® VM spray of heaven, black locust Broadleaf selective– especially legumes, Reclaim® Kudzu, sericea lespedeza, Durkin and Clopyralid smartweeds Transline® oxeye daisy, crown vetch Follansbee 2004a (Polygonaceae), and composites; foliar spray Alligare Fluroxypyr Woody and broadleaf Sericea lespedeza, musk Fluroxypyr Durkin 2009 Vista® XRT plants: foliar spray thistle, Japanese knotweed Non-selective—woody and Amur honeysuckle, autumn Accord® Concentrate herbaceous plants: foliar olive, Japanese Glyphosate Foresters® Non- Durkin 2011a spray, stump treatment, honeysuckle, garlic Selective stem injection mustard, multiflora rose Non-selective—invasives Aquamaster® Purple loosestrife, Glyphosate near open water; foliar Aquaneat® common reed, any species Durkin 2011a (aquatic) spray, cut stump Rodeo® near open water treatment, stem injection Durkin and Plateau® Imazapic Non-selective; foliar spray Leafy spurge Follansbee Alligare Panoramic 2SL 2004b Grasses, broadleaf weeds, Japanese knotweed, Arsenal®, Arsenal® AC vines, and brush species: Phragmites, purple Imazapyr Durkin 2011c Chopper®, Stalker® stump and/or basal-bark loosestrife, Johnson grass, treatment, foliar spray kudzu Metsulfuron Escort® XP, Oust® Broadleaf weeds and Klotzbach and Italian arum Methyl Oust® XP grasses: foliar spray Durkin 2004 Nepalese browntop, Sethoxydim Poast® Grass selective: foliar spray Canada bluegrass, bald Durkin 2001 brome Nepalese browntop, Arrow® 2EC Clethodim Grass selective: foliar spray Canada bluegrass, bald Durkin 2014 Envoy Plus® brome Chinese yam, kudzu, Amur Garlon® 3A Broadleaf selective: stump honeysuckle, autumn olive, Triclopyr Garlon® 4 and/or basal-bark Durkin 2011c sericea lespedeza, Alligare Triclopyr 4 treatment, foliar spot spray Japanese honeysuckle Stand Improvements The objective for the proposed stand improvements are to:

• maintain and restore the oak-hickory ecosystem resilience by reducing shade-tolerant understory competition, • create light conditions favorable for the establishment of oak-hickory regeneration, • improve forest structure through the creation of early successional habitat,

• reduce stressors caused by overstocked conditions; and improve and enhance the health, vigor, and growth of existing trees and native vegetation communities. Stand improvement activities could be employed in existing vegetation projects or as stand-alone projects. Generally, treatments would occur under the overstory in mature stands to remove undesirable species or in young stands to reduce competition. These activities are accomplished using manual treatments such as chainsaws, brushsaws, handsaws, axes, or application of herbicides directly to bark. Trees up to 9 inches diameter breast height (DBH) could be cut and felled, while trees greater than 9 inches DBH would be deadened in place to create a wildlife tree.

Cut-stump treatments would require cutting of trees or shrubs completely and applying herbicide directly to the stumps. Hack and squirt or stem-injection is applicable on stems greater than 1 inch and involves making incisions in the bark and applying herbicide into the incisions. Basal-bark typically is applicable to stems smaller than 6 inches and herbicide is applied directly to the bark.

As mentioned earlier on page 4, before treatment would occur, a site-specific interdisciplinary review would address any potential impacts to cultural resources, karst, threatened, endangered, or sensitive plants or animals, and other applicable resource areas. This review would be conducted using the Pretreatment Checklist Required for all Herbicide Treatment Areas (Shawnee Vegetation Management Strategy, Appendix B). We would apply herbicides during the time of year when the application methods are most effective. Cut-stump and stem-injection herbicide applications are most effective from June 1 to November 1, when sap flow is no longer heavy. Basal-bark treatment can be done any time of the year as long as stems are dry. Non-native Invasive Treatments Non-native invasive plant treatment methods would be based on the extent, location, type, and character of an infestation, and would be implemented using design criteria to increase effectiveness. A detailed description of current non-native invasive plant inventory, along with, treatments accomplished to date can be viewed in Appendix A of the Shawnee Vegetation Management EA and Tables 5a through 5f of this report. However, it is important to note that infestations constantly change and evolve, making it difficult to keep a current and complete inventory. It is certain that not all infestations are mapped and not all mapped locations are completely accurate, hence the need for a flexible and dynamic forest-wide approach.

Management priority of herbicide applications would be based on risk factors such as the number and size of known infestations, vectors for spread, proximity to susceptible habitat, threat to important resources (for example, wilderness, natural areas, imperiled species), ability to outcompete desirable plant species, and likelihood of success. These priorities would be used to select specific management activities for infestations. Table 2 describes the decision process or criteria that will be used to determine location of treatments and the treatment type, at a given site, in a given year.

Table 2. Decision Criteria for Herbicide Treatment of Non-Native Invasive Plants Priority Description Objective Early detection and rapid response to new Eradicate- treated (to the extent practical) species and/or new infestations. that no viable seed is produced over the Priority 1 Areas of high traffic and sources of infestation entire infestation and all plants have been (parking lots, trailheads, future or current eliminated during the current field season. vegetation restoration project areas)

Priority Description Objective Imperiled habitats (Natural Areas, barrens/glades, oak woodlands) Control of existing populations of aggressive Reduce- The infestation is treated to the Priority 2 non-native invasive species. extent that densities and/or rate of spread are reduced to the benefit of native plants and oaks. Control of reduction of existing populations of Contain- Portions of the infestation or Priority 3 native or non-native invasive species that do encroachment are treated to prevent not spread at an aggressive rate. spread of the weed beyond the perimeter of the infestation.

As mentioned earlier on page 4 of this document, prior to treatment, a site-specific interdisciplinary review would address any potential impacts to cultural resources, karst, threatened, endangered, or sensitive plants or animals, and other applicable resource areas. This review would be conducted using the Pretreatment Checklist Required for all NNIS Treatment Areas. We would apply commonly used, generally low-impact herbicides at or below label-recommended rates. We would follow all applicable state and federal laws. Herbicides likely to be used are listed in Table 1. We would follow all applicable state and federal laws. We would apply herbicides in accordance with the guidance published by the Illinois Nature Preserves Commission and The Nature Conservancy and monitor our use in compliance with the project design criteria, best management practices and direction in the Forest Service Manual (2900, 2109.14, 2150 and 2200). We would prepare a safety plan (FS Form-6700-7) prior to herbicide use and post signs to alert the public to the location and types of treatments being done and the date when a treated area could be re-entered.

We would apply herbicides during the time of year when application is most effective for a particular species and its life-cycle. If an application of herbicide is not as effective as expected, we would retreat as needed. We would ensure the re-establishment of native vegetation on a treated site through monitoring after invasives removal, and reseeding and/or planting native species, if necessary, to revegetate the site. Control techniques could vary, depending on the species, infestation size, or location. We based our proposed treatment methods on the recommendations of the USDA Forest Service management guides, USDA Natural Resource Conservation Service (NRCS) plants database, Illinois Nature Preserves Commission, as well as the River to River Cooperative Weed Management Area, The Nature Conservancy, scientific literature, the field experiences of Forest botanists and wildlife biologists, and discussions with invasive species experts.

Treatments of non-native invasive plants other than by herbicides would also be implemented when appropriate, as part of an integrated pest management strategy. Both manual and mechanical treatments may be used. Manual treatments involve the use of the hands alone or the hands with tools. They include pulling using the hands or weed-pulling tool, cutting/clipping; using cutting tools, grubbing; using a grub-hoe or similar tool, smothering; using appropriate, environmentally benign materials to cover targeted plants, and torching; and using a gas-flamed torch to scorch targeted plants. These methods are reasonably effective on smaller, herbaceous infestations. Mechanical treatments utilize machines, such as a using bulldozer or tractor with bushhog to remove targeted infestations. These methods would be employed to remove usually larger, densely growing, woody plants.

Design Criteria for the Action Alternative In order to minimize impacts on the environment and habitats from invasive species management and stand improvement, we would apply design criteria under the action alternative (Table 3). These criteria are based on requirements of Forest Service regulations, the Forest Plan, and US Fish and Wildlife Service requirements for managing federally listed species.

Table 3. Rare Plant Resources Design Criteria. Number Design Criteria Rationale Where non-native species are invading Mead’s milkweed occupied habitat, utilize control measures necessary to USFWS BO for the Forest Plan, p. 44, eradicate the undesirable species. To avoid adverse Integrated Pest Management of 1 effects on the milkweed, treatments should be done Mead’s milkweed during the dormant season – between the end of October Forest Plan, Appendix H, p. 285 and the end of March. Where necessary to protect rare plant resources survey • Forest Service Manual Policy, FSM areas to be treated with herbicides to locate rare plants 2670.32, Sensitive Species, “3. 2 prior to application. Have an applicator or individual who Avoid or minimize impacts to is familiar with rare plant resources and their habitats help species whose viability has been with searches. identified as a concern” • Forest Plan, Forest Wide Guideline, FW 26.5 (G), State of Illinois-Listed Threatened or Endangered Species, p. 43, “…activities should not jeopardize Protect rare plant resources, including Federal, Regional their continued existence on the Forester’s Sensitive Species, Species with Viability Forest.” 3 Evaluations, and State of Illinois-Listed Threatened and • Forest Plan, Forest Wide Endangered Species, from mechanical and/or chemical Guideline, FW 26.6 (G) Viability- treatments to the extent that is practical. Evaluation Species, p. 43, “They should be managed in accordance with management guidelines in Appendix H to ensure their continued existence on the Forest.”

Monitoring for the Action Alternative We will monitor our implementation of Alternative 2 in cooperation/collaboration with interested parties and the public to determine whether we are accomplishing expected outcomes (Table 4). If monitoring reveals unacceptable outcomes, we will implement appropriate measures to correct problems.

Table 4. Monitoring under Action Alternative Monitoring Activity Description Location and Timing Botanical Surveys to monitor native plant In selected treated areas following a Botanical Resources populations. growing season.

Monitor sites where rare species are known In treated areas within weeks (if rare plant to occur. Ensure that they are being is present during application) and again protected and habitat enhanced. during the next growing season.

Environmental Analysis Cumulative Impacts Spatial and Temporal Boundaries Spatial and temporal boundaries for Botanical Resources of the proposed action are described in Table 5.

Table 5. Spatial and temporal boundaries for rare botanical resources. Resource Boundary Rationale Spatial: The project area, which in this The effects of the proposal would be confined to the case is the Shawnee National Forest, as areas described. Botanical well as areas immediately adjacent to it. Temporal: 10 years in the past to a point Ten years before and after project implementation is 10 years post project implementation adequate to gauge management effects.

Past, Present and Reasonably Foreseeable Future Actions Past Actions: Past activities on National Forest System (NFS) lands and private lands in the project-area (the Forest) watersheds include, but are not limited to, farming, grazing and pesticide application; timber harvest; wild and prescribed fires; development and use of system and non-system equestrian and hiker trails; wildlife habitat management, including wildlife openings and pond construction; outdoor recreational use, including picnicking, hunting, fishing, horseback riding, hiking, boating, kayaking, use of all-terrain vehicles and off-highway vehicles; issuance of special-use permits; recreational facilities construction and maintenance; road construction, maintenance and use; tree- planting and stand improvements; power-line construction and maintenance and electrification of rural areas.

Present Actions: Many past activities in the project-area watersheds are still occurring. Present actions include, but are not limited to, trail reconstruction, maintenance and use; power-line maintenance; all- terrain vehicle/utility terrain vehicle use; timber harvest; agricultural management; pesticide application; prescribed and wild fire and fire suppression; use of trails; road maintenance and use; equestrian use; public visitation and outdoor recreation use (hiking and hunting).

Reasonably Foreseeable Future Actions: Activities similar to past activities on public and private lands are reasonably foreseeable in the future (Table 6). In the next 15 years, the Forest plans to continue to maintain roads and trails, issue special-use permits ranging from access-road and utility permits to outfitter-guide permits, suppress wildfires, harvest timber, apply pesticides, and conduct prescribed burning. Reasonably foreseeable future actions include those activities that are awaiting implementation, planned or listed in out-year schedules such as the Schedule of Proposed Actions or might be expected to occur in the area.

Table 6. Past, present and reasonably foreseeable future actions in the HUC 6 watersheds that contain National Forest land Action Scope of Action Agriculture (row-cropping) 252,052 acres Agriculture (pastureland) 249,280 acres Wildfires 100 acres per year Prescribed Burning 6,000-12,000 acres per year Timber Harvest/Stand Improvement About 3,000 acres per year All-Terrain Vehicle Use Variable use in watersheds Road Maintenance and Road Right of Way 300 miles per year Maintenance Tree Planting 500 acres per year Utility Right of Way Maintenance 250 miles per year Trail Maintenance 100 miles per year System Trails 472 miles Non-system Trails 100 miles Utility Line, driveways (Special-use Permits) 20 acres per year Invasive Species treatments using prescribed Fire 100 acres per year Invasive Species treatments using Mechanical 45 acres per year Invasive Species treatments using Chemicals 120 acres per year Openlands Management Mowing/disking 100 acres per year Trail Construction 10 miles per year Shoreline Stabilization 0.59 miles Gully Stabilization 0.6 miles per year Residential Development 2,000 house per decade National Forest Land 286,313 acres Non-National Forest Land 1,233,105 acres

The Shawnee National Forest has several signed decisions that authorize herbicide application for the treatment of non-native invasive plants, stand improvement, and tree and shrub removal. Table 7 lists those projects, as well as the treatments and acres authorized by each.

Table 7. Existing Projects Authorizing Herbicide Use on the Shawnee National Forest Project Name Description Acres Treatment of all known sites of four highly invasive species (3,289 ac), Invasive Species cut and stump-spray and/or girdle some native trees and shrubs on 20,338 Management EA about 275 acres, and treatment of all invasive plants within 23 natural areas (16,774 ac). Cretaceous Hills Ecological Treatment of new and existing infestations of invasive species within 15,139 Restoration EIS the project area.

Project Name Description Acres Big Muddy River Bottoms Treatment of stumps for stand improvement activities and treatment 12,146 Habitat Improvement II EA of invasive plants within the project area. Phragmites and Reed Treatment of known and future infestations of these two invasive 103 Canarygrass Management EA species anywhere on the forest. Lee Mine Hardwood Grass specific herbicides can be applied as need to protect sensitive 1,402 Restoration EA plants from Nepalese browntop infestations. Waterfall Stewardship Pilot Herbicide use to treat non-native invasive plant infestations within 560 Project EA the project area and for stand improvement. A total of 49,688 acres across the Shawnee National Forest is authorized for herbicide use from these decisions. In addition, herbicides can be used to treat invasive plant infestations and other weedy vegetation at administrative and developed recreation sites on 2,189 acres across the Forest. Therefore, herbicide use is authorized on 51,877 acres of the Forest’s 289,000 acres, about 18% of the Shawnee National Forest’s total acreage.

Regional Forester’s Sensitive Plants Evaluated The Shawnee National Forest has 95 RFSS (sensitive or Regional Forester’s Sensitive) plants and recorded on its lands. The proposed action covers the entire Shawnee National Forest, so all RFSS plants were evaluated for this project. Table 7 lists these plants, as well as the counties where they have been found on the Forest.

Table 8. Regional Forester’s Sensitive Plant Species (RFSS) documented as present or historically present in the 11 counties of southern Illinois where there are lands managed by the Shawnee National Forest. Counties indicated as: A = Alexander, G = Gallatin, H = Hardin, Ja = Jackson, Jo = Johnson, M = Massac, P = Pope, Pu = Pulaski, S = Saline, U = Union, and W = Williamson. Scientific Name Common Name Counties 1. Actaea rubifolia Appalachian bugbane G, H, Ja, Jo, M*, P, S 2. Amorpha nitens shining false indigo A, M, P, S 3. Aronia melanocarpa black chokeberry Jo, S 4. Asplenium bradleyi Bradley's spleenwort Ja, S, U 5. Asplenium resiliens blackstem spleenwort A*, Ja, U 6. Bartonia paniculata twining screwstem Jo*, P 7. Berchemia scandens Alabama supplejack S 8. Botrychium biternatum sparselobe grapefern A, G, H, Ja*, Jo, P, Pu*, S, U* 9. Bromus nottowayanus Nottoway Valley brome Ja, P 10. Buchnera americana American bluehearts Ja, P 11. Calamagrostis porteri ssp. insperata Porter’s reedgrass P 12. Carex alata broadwing sedge Ja*, M*, P 13. Carex atlantica prickly bog sedge P 14. Carex bromoides brome-like sedge Ja, Jo, P 15. Carex cherokeensis Cherokee sedge A, H, Ja, U 16. Carex decomposita cypress-knee sedge G*, Jo, P, Pu, U 17. Carex gigantea giant sedge Ja, Jo, M, Pu, U 18. Carex intumescens greater bladder sedge A, Ja, Jo. P, Pu, S 19. Carex lupuliformis false hop sedge A*, H*, Ja, Jo*, M*, P*, Pu*, S*, U* 20. Carex nigromarginata black edge sedge A, G, H, Ja, P*, U 21. Carex oxylepis var. pubescens sharpscale sedge H

Scientific Name Common Name Counties 22. Carex prasina drooping sedge Jo, M*, P 23. Carya pallida sand hickory A, H, U 24. Chamaelirium luteum fairywand H, M, P 25. Chelone obliqua var. speciosa red turtlehead A*, G*, Ja*, Jo*, M*, P*, U* 26. Chimaphila maculata striped prince’s pine H, P 27. Cirsium carolinianum soft thistle H*, Ja*, P, S 28. Cladrastis kentukea Kentucky yellowwood A, G* 29. Cynosciadium digitatum finger dogshade Ja 30. Cyperus lancastriensis manyflower flatsedge M*, P, Pu, S 31. Cypripedium parviflorum var. greater yellow lady’s slipper A, G, Ja, Jo, M, P, U, W pubescens 32. Dennstaedtia punctilobula eastern hay-scented fern Jo, P 33. Dichanthelium joorii** variable panic grass Jo, M*, U 34. Dichanthelium ravenelii Ravenel's rosette grass H, P, U* 35. Dichanthelium yadkinense** Yadkin's panic grass G, Jo*, P 36. Dirca palustris Eastern leatherwood Ja, Jo, P 37. Dodecatheon frenchii French's shootingstar Ja, Jo, P, S, U, W 38. Dryopteris goldieana Goldie’s woodfern Ja, Jo, P, U, W 39. Eleocharis wolfii Wolf's spikerush G, Ja, M, P, S, U 40. Eryngium prostratum creeping eryngo A, M, P, S, W 41. Eupatorium hyssopifolium hyssopleaf thoroughwort Jo, P 42. Gentiana alba plain gentian A, Ja, M, P 43. Glyceria arkansana Arkansas mannagrass A, Ja, Jo, U 44. Helianthus angustifolius swamp sunflower M, P 45. Heteranthera reniformis kidneyleaf mudplantain A*, P, U* 46. Hexalectris spicata spiked crested coralroot H, Ja*, P* 47. Hottonia inflata American featherfoil Ja, Jo, P, S, U 48. Huperzia porophila rock clubmoss A*, G, Ja*, Jo, M*, P, S, U* 49. Hydrastis canadensis goldenseal A, G, H, Ja, Jo, M, P, Pu, S, U, W 50. Hydrolea uniflora one-flowered false fiddleleaf A*, Ja, Jo, M*, U 51. Hylotelephium telephioides Allegheny stonecrop G, H, Ja, P, S 52. Isotria verticillata large whorled pogonia P 53. Juglans cinerea butternut A, H, Ja, Jo, M, P, S, U 54. Lilium superbum Turk’s-cap lily G, H, Ja, Jo, P, W 55. Lonicera dioica var. glaucescens** limber honeysuckle Ja 56. Lonicera flava yellow honeysuckle Ja, P 57. Malus angustifolia southern crab apple Ja*, M, P, Pu 58. Melothria pendula Guadeloupe cucumber A, H, Ja, Jo, M, P, U 59. Oxalis illinoensis Illinois wood sorrel H, Ja, P 60. Panax quinquefolius American ginseng A, G, H, Ja, Jo, M, P, S, U, W 61. Penstemon tubaeflorus white wand beardtongue A, Ja*, M*, P*, S*, U* 62. Phaeophyscia leana wreath lichen G, H, M, P 63. Phemeranthus parviflorus sunbright Jo, M, P, U 64. Plantago cordata heartleaf plantain Ja, Jo, P, S 65. Platanthera clavellata small green wood orchid P 66. Platanthera flava var. flava palegreen orchid Jo, M, P, U

Scientific Name Common Name Counties 67. Poa alsodes grove bluegrass Ja, P* 68. Polygala incarnata procession flower M*, P 60. Polytaenia nuttallii Nuttall’s prairie parsley G*, Ja*, Jo*, P*, S*, U* 70. Quercus montana chestnut oak A, G, H, Ja, S, U 71. Rhexia mariana Maryland meadowbeauty Ja*, M, P, S, W 72. Rhynchospora glomerata clustered beaksedge Jo, P 73. Rudbeckia fulgida var. sullivantii Sullivant's coneflower H*, P* 74. Sagittaria australis longbeak arrowhead P, U* 75. Sanicula smallii Small’s blacksnakeroot H 76. Saxifraga virginiensis early saxifrage H 77. Scirpus polyphyllus leafy bulrush H, M, P 78. Scleria oligantha little nutrush H 79. Scleria pauciflora fewflower nutrush H, Ja, Jo, M, P, U, W 80. Silene ovata Blue Ridge catchfly H 81. Silphium trifoliatum whorled rosinweed H* 82. Spiranthes vernalis spring lady’s tresses Ja, Jo, M*, P, S, U*, W 83. Stellaria pubera star chickweed H, P 84. Stenanthium gramineum eastern featherbells G, Ja, Jo, M*, P, Pu, U 85. Styrax americanus American snowbell A, Ja, Jo, M, P, U 86. Styrax grandifolius bigleaf snowbell A, P, Pu 87. Synandra hispidula Guyandotte beauty Ja, W 88. Thelypteris noveboracensis New York fern P 89. Torreyochloa pallida pale false mannagrass Ja, U 90. Tragia cordata heartleaf noseburn G, H, Jo, P 91. Trichomanes boschianum Appalachian bristle fern G* H, Jo, P, U 92. Trifolium reflexum buffalo clover G*, Ja, Jo 93. Trillium viride wood wakerobin Ja, U, W* 94. Triphora trianthophora threebirds A, Ja, Jo, S, U 95. Vaccinium stamineum deerberry H, P* * species extirpated in that county ** Mohlenbrock’s (2014) nomenclature; all other nomenclature from the PLANTS database (2019)

Shawnee National Forest RFSS Plant Habitats RFSS plants on the Shawnee National Forest can be grouped by the habitats in which they are found. The following habitat types list RFSS plants found in them, as well as the number of known locations on the Forest and the months in which they flower. More detailed information about these species is provided in Appendix 1 of this document. Acid Gravel Seeps, Woods Adjacent to Seeps, and Springs • Bartonia paniculata (twining screwstem) (6) Aug-Sep • Carex atlantica (prickly bog sedge) (8) May • Carex bromoides (brome-like sedge) (5) Apr-May • Carex prasina (drooping sedge) (1) (May-Jun) • Helianthus angustifolius (swamp sunflower) (4) Aug-Oct • Isotria verticillata (large whorled pogonia) (2) May-Jun

• Platanthera clavellata (small green wood orchid) (4) Jun-Aug • Rudbeckia sullivantii (Sullivant’s coneflower) (2) Jul-Oct • Scirpus polyphyllus (leafy bulrush) (9) Jul-Sep • Thelypteris noveboracensis (New York fern) (1) Jun-Sep Forested Wetlands and Swamps • Carex decomposita (cypress-knee sedge) (2) Jun-Aug • Carex gigantea (giant sedge) (2) May-Aug • Carex intumescens (greater bladder sedge) (2) May-Sep • Carex lupuliformis (false hop sedge) (3) Jun-Oct • Chelone obliqua var. speciosa (red turtlehead) (1) Aug-Oct • Cynosciadium digitatum (finger dogshade) (1) May-Jun • Dichanthelium joorii (variable panic grass) (2) Jun-Oct • Eleocharis wolfii (Wolf’s spikerush) (2) May-Jul • Glyceria arkansana (Arkansas manna grass) (4) May-Jun • Heteranthera reniformis (kidneyleaf mudplantain) (1) Jul-Aug • Hottonia inflata (American featherfoil) (3) Jun-Aug • Hydrolea uniflora (one-flowered false fiddleleaf) (3) Jun-Sep • Plantanthera flava var. flava (palegreen orchid) (4) Jun-Aug • Sagittaria australis (longbeak arrowhead) (2) Jul-Oct • Styrax americanus (American snowbell) (1) Apr-May • Torreyochloa pallida (pale false mannagrass) (2) May-Aug • Triphora trianthophora (threebirds) (2) Aug-Oct Floodplain and Riparian Forests, Lakes, Ponds, Creeks, and Other Mesic Areas • Amorpha nitens (shining false indigo) (2) May-Jun • Carex alata (broadwing sedge) (2) May • Carex cherokeensis (Cherokee sedge) (2) (May-Sep) • Cyperus lancastriensis (manyflower flatsedge) (1) Aug-Oct • Dichanthelium yadkinense (Yadkin’s panic grass) (9) May-Sep • Eryngium prostratum (creeping eryngo) (1) May-Nov • Lilium superbum (Turk’s-cap lily) (16) Jul • Oxalis illinoensis (Illinois woodsorrel) (10) Jun-Sep • Phaeophyscia leana (wreath lichen) (1) • Plantago cordata (heartleaf plantain) (8) Apr-Jul • Rhexia mariana (Maryland meadowbeauty) (8) Jun-Sep • Rhynchospora glomerata (clustered beaksedge) (5) Jul-Oct • Stellaria pubera (star chickweed) (4) Mar-May • Stenanthium gramineum (eastern featherbells) (8) Jun-Aug • Tragia cordata (heartleaf noseburn) (3) Jul-Sep • Trillium viride (green trillium) (1) Apr Open Barrens, Prairies, Glades, and Fields • Buchnera americana (American bluehearts) (1) Jun-Sep

• Bromus nottowayanus (Nottoway Valley brome) (2) Jun-Aug • Cirsium carolinianum (Carolina thistle) (8) Jun-Jul • Eupatorium hyssopifolium var. hyssopifolium (hyssopleaf thoroughwort) (1) Aug-Nov • Malus angustifolius (southern crab apple) (2) May • Melothria pendula (Guadeloupe cucumber) (~12) Jun-Sep • Penstemon tubaeflorus (white wand beardtongue) (3) Jun • Phemeranthus parviflorus (sunbright) (12) Jun-Jul • Polygala incarnata (procession flower) (5) Jun-Aug • Polytaenia nuttallii (prairie parsley) (12) Apr-Jun • Scleria oligantha (littlehead nutrush) (1) Jun-Sep • Scleria pauciflora (fewflower nutrush) (12) Jun-Sep • Silphium trifoliatum (whorled rosinweed) (2) Jul-Sep • Spiranthes vernalis (spring lady’s tresses) (7) Jul-Aug • Trifolium reflexum (buffalo clover) (2) May-Jul Cliff Tops, Cliff Faces, Cliff Bases, and Rich Slopes of Cliffs • Actaea rubifolia (Appalachian bugbane) (25) Jul-Oct • Aronia melanocarpa (Black chokecherry) (1) May-Jun • Asplenium bradleyi (Bradley’s spleenwort) (5) • Asplenium resiliens (Black-stem spleenwort) (2) • Botrychium biternatum (sparselobe grapefern) (20+) • Calamagrostis porteri ssp. insperata (Porter’s reedgrass) (4) • Carya pallida (sand hickory) (4) Apr-May • Dennstaedtia punctilobula (eastern hay-scented fern) (4) Jul-Oct • Dodecatheon frenchii (French’s shootingstar) (25+) Apr-May • Huperzia porophila (rock clubmoss) (8) Jun-Sep • Hylotelephium telephioides (Allegheny stonecrop) (13) Aug-Sep • Lonicera dioica var. glaucescens (limber honeysuckle) (2) May-Jun • Lonicera flava (yellow honeysuckle) (4) Apr-May • Saxifraga virginiensis (early saxifrage) (6) Apr-Jun • Trichomanes boschianum (Appalachian bristle fern) (12) • Vaccinium stamineum (deerberry) [also dry-mesic upland woods] (2) May-Jun Xeric, Dry, and Dry-Mesic Upland Woods, and Pine Plantations • Berchemia scandens (supplejack) (1) Apr-Jun • Carex nigromarginata (black-edge sedge) (13) Apr-May • Carex oxylepis var. pubescens (sharpscale sedge) (5+) Apr-May • Chamaelirium luteum (fairywand) (8) May-Jun • Chimaphila maculata (spotted wintergreen) (6) Jun-Jul • Cypripedium parviflorum var. pubescens (greater yellow lady’s slipper) (16) Apr-Aug • Cirsium carolinianum (Carolina thistle) (8) Jun-Jul • Dichanthelium ravenelii (Ravenel’s rosette grass) (4) Jun-Oct • Gentiana alba (plain gentian) (2) mid-Aug-Oct • Hexalectris spicata (spiked crested coralroot) (6) Jun-Sep

• Poa alsodes (grove bluegrass) (1) May-Jun • Polytaenia nuttallii (prairie parsley) (12) Apr-Jun • Quercus montana (chestnut oak) (9) Apr-May • Sanicula smallii (Small’s blacksnakeroot) (1) Jul • Silene ovata (Blue Ridge catchfly) (5) Aug Dry-Mesic and Mesic Upland Woods, Hollows, and Ravines • Botrychium biternatum (sparselobe grapefern) (20+) • Cladrastis kentukea (Kentucky yellowwood) (1) May • Dirca palustris (Eastern leatherwood) (4) Apr-May • Dryopteris goldieana (Goldie’s woodfern) (2) Jun-Sep • Hydrastis canadensis (Goldenseal) (widespread) Apr-May • Juglans cinerea (Butternut) (uncommon) Apr-May • Panax quinquefolius (American ginseng) (widespread) Jun-Jul • Styrax grandifolius (Bigleaf snowbell) (2) May • Synandra hispidula (Guyandotte beauty) (3) May-Jun Environmental Impacts to Plants RFSS plants are grouped by habitat for this analysis Acid Gravel Seeps, Woods Adjacent to Seeps, and Springs Current Condition and Expected Future Conditions Most populations of sensitive plants found in seep and seep spring habitats on the Forest are threatened by non-native invasive plants and/or by habitat degradation from woody encroachment. Because of that, two NEPA decisions (Invasive Species Management and Cretaceous Hills Ecological Restoration Project) were signed that authorized management action to preserve them. Treatments allowed are—integrated pest management of non-native invasive plants, including herbicide treatments; removal of encroaching woody vegetation, some sites with herbicide and others without it; and prescribed fire. Recently implemented treatments have shown promising results in reducing non- native invasive plant infestations near vulnerable plants and in improving their habitat. Some sensitive plant occurrences have increased in numbers following prescribed fire and herbicide control of non- native invasive plant infestations.

Two locations of sensitive plants growing in seeps and springs are not authorized for treatment under currently signed decisions. An occurrence of brome-like sedge was last observed in 2005 at a natural area; whether invasive plants were present at that time was not noted. The only location of drooping sedge known on the Forest was last observed in 2017; no invasive plants were found near this occurrence. Although invasive infestations were either not noted or not found at these locations, it is probably only a matter time before non-native invasive plants reach these sites. Nepalese browntop has spread across the Forest in the last few of decades and has reached all but a few of the known seep springs. Should this invasive grass reach those sites, only manual or mechanical methods could be used to treat it. Control would be time consuming and inefficient, making it less likely that treatments would take place. Those populations could potentially to decline over time. Drooping sedge would be under particular threat, since there is only one known population on the Forest.

Non-native invasive plant infestations can be herbicide treated at the majority of sensitive plant populations located at seep springs, but treatment may not be authorized for some non-native invasive plant species. The two NEPA decisions covered non-native invasive plants known to be in their project areas when the analyses took place. If a non-native invasive plant that was not analyzed for either of the two NEPA projects becomes a threat, those infestations could not be treated with herbicides. EDRR treatments to control new species would be hampered with that restriction, making treatment less likely to be implemented and probably less effective if it does. Sensitive plants growing in this habitat type could potentially be threatened by these types of infestations.

Threats from non-native invasive plants are likely to increase in the future. The spread of invasive plants is expected to accelerate, in large part due to climate change. Increased disturbance and erosion from extreme rainfall, flooding, drought, wildfires, and high winds will create habitat that invasive plants would be very likely to invade. All sensitive plants, including those growing in and around seep springs, would potentially be under greater threat from invasive plants in the future.

Most seep spring sites with sensitive plants on the Forest are authorized for treatments to control encroaching native woody vegetation. However, herbicide use to control woody vegetation is not allowed at several locations. Some cut vegetation that would not be herbicide treated is likely to resprout, making control more difficult. Habitat restoration for sensitive plants may not be as effective as it could be without the option of herbicide use. If treatments are frequently repeated, trampling could result in more soil compaction.

To summarize, since all but a couple of seep spring inhabiting sensitive plant populations on the Forest are located at sites where herbicide treatments of invasive infestations are allowed, as needed, there should be relatively few negative consequences from the no action alternative. However, two sensitive plant populations are in locations where herbicide use is not allowed. Those species would be under greater threat from non-native invasive plant infestations, especially drooping sedge, which has only one known population on the Forest. Also, non-native invasive plant species not analyzed in previous NEPA decisions could not be treated with herbicides, making EDRR control more difficult. These non- native invasive plant species may pose a threat to all sensitive plants found in this habitat on the Forest, especially in the future when the spread of non-native invasive plants will likely accelerate due to climate change. Finally, control of encroaching woody vegetation may not be as effective at sites where herbicide use is not allowed. Frequently repeated treatments may be necessary to effectively restore habitat for sensitive plants at those locations and would also increase soil compaction. With limited funding and personnel, fewer sites are likely to be treated.

Alternative 2-Proposed Action Direct and Indirect Impacts There should be no adverse direct impacts to sensitive species located in seep springs if alternative 2 is chosen. Implementation of design criteria would ensure that sensitive plant species would be protected from harm if herbicide is used for non-native invasive plant control and/or stand improvement. Infestations not analyzed in previous decisions would be reviewed by a botanist before herbicide treatment is implemented.

There should be beneficial indirect impacts to seep spring inhabiting sensitive plants. Implementation of the proposed action would help slow the rate at which invasive species are spreading across the Forest

17 and could prevent many of them from reaching sensitive plants at seep springs. The process to further authorize treatments of invasive plant infestations with herbicides would be greatly streamlined. It would be far easier to control species new to the Forest using EDRR, which should do much to prevent them from becoming widespread. Satellite infestations of existing infestations would be easier to treat in a timely manner. Rapid treatment of infestations at locations not currently authorized for treatment would be possible. Trees and shrubs threatening seep spring habitat could be treated more efficiently with herbicide at more locations. Cumulative Impacts Table 6 lists past, present, and reasonably foreseeable future actions, most of which affect the spread of non-native invasive plants on the Shawnee National Forest. Adjacent agricultural lands that are farmed and grazed will continue to be sources of invasive infestations that spread into the Forest. Non- agricultural private residences will be a source, as well as new residential construction sites. Rights-of- way, such as roads and utility lines will function as corridors for invasive species spread, as will system and non-system trails, roads and driveways permitted for the use of private landowners. Visitor recreation, such as horseback riding, hiking, hunting, boating, kayaking, and illegal ATV use, will be a continuing source of invasive plant infestations. Wildfires will also affect the spread of invasives, the effects depending on the specific non-native invasive plants present.

Forest management will continue to affect the spread of invasive plants, with some actions accelerating the spread and others decreasing it. Trail construction, firelines, and access paths for gully and shoreline stabilization will increase disturbed corridors that non-native invasive plants can invade and spread. Increased disturbance at active timber harvest sites will also increase disturbed sites within the Forest. Maintenance of openlands using mowing and disking will increase disturbance. On the other hand, integrated pest management will provide control of some invasive plant infestations. Prescribed fires, especially those taking place repeatedly at specific sites, will suppress several non-native invasive plant species on the Forest. Herbicide, manual, and mechanical treatments have provided increased control of selected infestations across the Forest; future treatments will provide continued control.

The Shawnee National Forest has signed several decisions authorizing herbicide use (Table 7). Those decisions allow herbicide treatment on about 18% of the Shawnee National Forest. Increased herbicide use has reduced the spread of non-native invasive plants on the Forest. The Invasive Species Management and Cretaceous Hills Ecological Restoration projects authorized treatments to protect seep spring sensitive plants and their habitats, not just through herbicide treatments, but with tree and shrub removal and prescribed fire. Herbicide treatments, prescribed fire, and mechanical removal trees and shrubs have already improved habitat seep spring habitat at several sites. Future treatments should continue and expand to additional sites where allowed, restoring habitat and benefitting sensitive plants at those sites.

Implementation of the proposed action would have beneficial cumulative impacts to sensitive plant species found in seep spring habitat. It would enhance and expand herbicide treatments across the Forest, not just 18% of it, slowing their spread and making it less likely that new infestations would reach sensitive plants growing in seep spring habitats. Herbicide use could be expanded to seep spring locations where herbicide use to treat non-native invasive plants and/or encroaching woody vegetation is not allowed. Along with prescribed fire, habitat at those sites would have a greater likelihood of being restored. Controlling non-native invasive plants and woody encroachment with herbicide is more

18 efficient and effective, so habitat restoration could potentially take place at more sites on the Forest. Sensitive plant populations growing in seep spring habitats would be more likely to be preserved and may even increase in numbers. Therefore, implementation of the proposed project would have beneficial impacts to sensitive plants growing in this habitat type. Forested Wetlands and Swamps Current Condition and Expected Future Conditions Many populations of sensitive plants found in forested wetlands and swamps on the Forest are threatened by non-native invasive plants and/or by habitat degradation from woody encroachment. Several NEPA decisions (Invasive Species Management, Cretaceous Hills Ecological Restoration Project, and Big Muddy Bottomlands Habitat Improvement I & II) were signed that authorized management action to preserve them. Treatments allowed are—integrated pest management of non-native invasive plants, including herbicide treatments; control of encroaching woody vegetation, some sites with herbicide and others without it; and prescribed fire. Recently implemented treatments have shown promising results in reducing non-native invasive plant (non-native invasive plant) infestations near vulnerable plants and in improving their habitat.

About a third of the sensitive plants populations found in forested wetlands and swamps of the Forest are located at sites that are not authorized for treatment under currently signed decisions. For example, many of those populations are found at the Grantsburg Swamp Ecological Area. Autumn olive, bush honeysuckle, and Japanese honeysuckle were observed in the bottomland forest near the swampy area during 2018 monitoring, apparently spreading from the woodlands near the bluffs. Those woodlands are near private residences. Trying to control these woody invasives would be time consuming and inefficient; a crew could remove only a few acres on any given day. Since Grantsburg Swamp Ecological Area is 788 acres, most of those infestations would probably not be treated. American snowbell would be under particular threat, since the only known population on the Forest is located in this natural area. Expanding bush honeysuckle and Japanese honeysuckle could not only compete with this tree but could also alter its bottomland forest habitat.

Non-native invasive plant infestations can be herbicide treated at most sensitive plant populations located at forested wetlands and swamps, but treatment may not be authorized for some non-native invasive plant species. Two of the NEPA decisions covered non-native invasive plants known to be present in their project areas when the analyses took place (the Big Muddy Bottomlands II decision also covered non-native invasive plants not known but likely to be present at Oakwood Bottoms and surrounding woodlands). If a non-native invasive plant that was not authorized for herbicide treatment becomes a threat, those infestations could not be treated with herbicides. EDRR treatments to control new species would be hampered with that restriction, making treatment less likely to be implemented and probably less effective if it does. Sensitive plants growing in this habitat type outside of the Big Muddy II project area could potentially be threatened by these types of infestations.

Threats from non-native invasive plants are likely to increase in the future. The spread of invasive plants is expected to accelerate, in large part due to climate change. Increased disturbance and erosion from extreme rainfall, flooding, drought, wildfires, and high winds will create habitat that invasive plants would be very likely to invade. All sensitive plants, including those growing in forested wetlands and swamps, would potentially be under greater threat from invasive plants in the future.

Over half of the known sites of sensitive plants found in forested wetlands and swamps on the Forest are authorized for treatments to control encroaching native woody vegetation with herbicide, as well as with prescribed fire. Several of these sensitive plants require open canopy habitat and are being threatened by forest succession. It is especially difficult to control shade tolerant trees that grow in wet and bottomland habitats, such as maple, box elder, and ash. These trees can re-sprout vigorously unless they are treated with herbicide. They are also less likely to be controlled by prescribed fire. A sensitive plant that is especially threatened by woody encroachment is red turtlehead, which is found in only one natural area where no habitat restoration treatments have been authorized and where forest succession has altered its habitat.

To summarize, many of the known swamp and forested wetland sensitive plant populations on the Forest are located at sites where herbicide treatments are allowed. There should be relatively few negative consequences from the no action alternative for those populations. However, about a third of those sensitive plant populations are in locations where herbicide use is not allowed. They remain under greater threat from non-native invasive plant infestations, especially in the future when the spread of non-native invasive plants will likely accelerate due to climate change. Also, non-native invasive plant species not analyzed in most previous NEPA decisions could not be treated with herbicides, making EDRR control more difficult. These non-native invasive plant species may pose a threat to all but a few sensitive plants growing in wetland habitats on the Forest. Finally, control of encroaching woody vegetation may not be as effective at sites where herbicide use is not allowed; frequently repeated treatments may be necessary to effectively restore habitat for sensitive plants at those locations. With limited funding and personnel, fewer sites are likely to be treated. Alternative 2-Proposed Action Direct and Indirect Impacts There should be no adverse direct impacts to sensitive species located in forested wetlands and swamps if alternative 2 is chosen. Implementation of design criteria would ensure that sensitive plant species would be protected from harm if herbicide is used for non-native invasive plant control and/or treatment of woody encroachment. Infestations not analyzed in previous decisions would be reviewed by a botanist before herbicide treatment is implemented.

There should be beneficial indirect impacts to sensitive plants that grow in forested wetlands and swamps. Implementation of the proposed action would help slow the rate at which invasive species are spreading across the Forest and could prevent many of them from reaching sensitive plants in these habitats. The process to further authorize treatments of invasive plant infestations with herbicides would be greatly streamlined. It would be far easier to control species new to the Forest using EDRR, which should do much to prevent them from becoming widespread. Satellite infestations of existing infestations would be easier to treat in a timely manner. Rapid treatment of infestations at locations not currently authorized for treatment would be possible. Trees and shrubs threatening populations of sensitive plants could be treated more efficiently with herbicide at more locations. Cumulative Impacts Table 6 lists past, present, and reasonably foreseeable future actions, most of which affect the spread of non-native invasive plants on the Shawnee National Forest. Adjacent agricultural lands that are farmed and grazed will continue to be sources of invasive infestations that spread into the Forest. Non- agricultural private residences will be a source, as well as new residential construction sites. Rights-of-

20 way, such as roads and utility lines function as corridors for invasive species spread, as do system and non-system trails, and roads and driveways permitted for the use of private landowners. Visitor recreation, such as horseback riding, hiking, hunting, boating, kayaking, and illegal ATV use, will be a continuing source of invasive plant infestations. Wildfires will also affect the spread of invasives, the effects depending on the specific non-native invasive plants present.

Forest management will continue to affect the spread of invasive plants, with some actions accelerating the spread and others decreasing it. Trail construction, firelines, and access paths for gully and shoreline stabilization will increase disturbed corridors that non-native invasive plants can invade and spread. Increased disturbance at active timber harvest sites will also increase sites where non-native invasive plants are likely to invade and spread within the Forest. Maintenance of openlands using mowing and disking will also increase disturbance. On the other hand, integrated pest management will provide control of some invasive plant infestations. Prescribed fires, especially those taking place repeatedly at specific sites, will suppress several non-native invasive plant species. Herbicide, manual, and mechanical treatments of non-native invasive plants have provided increased control of selected infestations across the Forest; future treatments will provide continued control.

The Shawnee National Forest has signed several decisions authorizing herbicide use (Table 7). Those decisions allow herbicide treatment on about 18% of the Shawnee National Forest. Increased herbicide treatment has already reduced the spread of many non-native invasive plant infestations on the Forest. Several projects authorized treatments to protect sensitive plants that grow at forested wetlands and swamps and to restore their habitats, not just through herbicide treatments, but also with tree and shrub removal and prescribed fire. Herbicide treatments have already reduced non-native invasive plant infestations at several sensitive plant locations. Future treatments should continue and expand to additional sites, restoring habitat and benefitting sensitive plants in more locations.

Implementation of the proposed action would have beneficial cumulative impacts to sensitive plant species found forested wetlands and swamps. It would enhance and expand herbicide treatments across the Forest, not just 18% of it, slowing their spread and making it less likely that new infestations would reach sensitive plants growing in forested wetlands and swamps. Herbicide use could be expanded to locations where herbicide use to treat non-native invasive plants and/or encroaching woody vegetation is not currently allowed. Along with prescribed fire, habitat at those sites would have a greater likelihood of being restored. Controlling non-native invasive plants and woody encroachment with herbicide is more efficient and often more effective than manual and mechanical control, so habitat restoration could potentially take place at more sites on the Forest. Sensitive plant populations growing in these habitats would be more likely to be preserved and may even increase in numbers. Therefore, implementation of the proposed project would have beneficial impacts to sensitive plants growing in forested wetlands and swamps. Floodplain and Riparian Forests, Lakes, Ponds, Creeks, and Other Mesic Areas Current Condition and Expected Future Conditions Many populations of sensitive plants found in floodplain and riparian forests, lakes ponds, creeks and other mesic areas on the Forest are threatened by non-native invasive plants and/or by habitat degradation from woody encroachment. Several NEPA decisions (Invasive Species Management, Cretaceous Hills Ecological Restoration Project, and Big Muddy Bottomlands Habitat Improvement I & II) were signed that authorized management action to preserve them. Treatments allowed are—

21 integrated pest management of non-native invasive plants, including herbicide treatments; control of encroaching woody vegetation, some sites with herbicide and others without it; and prescribed fire. Recently implemented treatments have shown promising results in reducing non-native invasive plant infestations near vulnerable plants and in improving their habitat.

Less than half of the sensitive plants populations found in these habitat types on the Forest are located at sites that are authorized for herbicide treatment under currently signed decisions. Although non- native invasive plant infestations can be herbicide treated at some sensitive plant populations in these habitats, treatment may be authorized for only a few non-native invasive plant species. Two of the NEPA decisions covered non-native invasive plants known to be present in their project areas when the analyses took place (the Big Muddy Bottomlands II decision also covered non-native invasive plants not known but likely to be present at Oakwood Bottoms and surrounding woodlands). If a non-native invasive plant that was not authorized for herbicide treatment becomes a threat, those infestations could not be treated with herbicides. EDRR treatments to control new species would be hampered with that restriction, making treatment less likely to be implemented and probably less effective if it does. Sensitive plants growing in these habitats type outside of the Big Muddy II project area could potentially be threatened by these types of infestations.

Threats from non-native invasive plants are likely to increase in the future. The spread of invasive plants, in large part due to climate change. Increased disturbance and erosion from extreme rainfall, flooding, drought, wildfires, and high winds will create habitat that invasive plants would be very likely to invade. All sensitive plants, including those growing in these habitat types, would potentially be under greater threat from invasive plants in the future.

Less than half of the known sites of sensitive plants found in floodplain and riparian forests, lakes ponds, creeks and other mesic areas on the Forest are authorized for treatments to control encroaching native woody vegetation with herbicide and/or with prescribed fire. Several of these sensitive plants require open canopy habitat and are being threatened by forest succession. It is especially difficult to control shade tolerant trees that grow in mesic habitats, such as maple, box elder, and ash. These trees can resprout vigorously unless they are treated with herbicide. They are also less likely to be controlled by prescribed fire. Because of climate change, total rainfall should increase, accelerating forest succession and woody encroachment in the future at these habitat types.

A sensitive plant that is especially threatened by woody encroachment is creeping eryngo; it was present at only one natural area near a pond. Woody encroachment is the greatest threat to creeping eryngo’s habitat, herbicide use is only authorized there to treat common reed (Phragmites australis). Some trees and shrubs have been cut manually at the site but are likely to resprout after treatments. Having to cut trees and shrubs over and over again at this site would increase trampling and soil compaction. Fewer sites are likely to be treated with limited funding and personnel.

To summarize, most of the known sensitive plant populations that grow in floodplain and riparian forests, lakes ponds, creeks and other mesic areas on the Forest are located at sites where herbicide treatments are not allowed. Those populations remain under threat from non-native invasive plant infestations. Also, non-native invasive plant species not analyzed in most previous NEPA decisions could not be treated with herbicides, making EDRR control more difficult. These non-native invasive plant species may pose a threat to all but a few sensitive plants growing in these habitats on the Forest. Control of encroaching woody vegetation may not be as effective at sites where herbicide use is not

22 allowed and could cause some damage. Frequently repeated treatments may be necessary to effectively restore habitat for sensitive plants at those locations, potentially damaging plant habitat from soil compaction. With limited funding and personnel, fewer sites are likely to be treated. Finally, sensitive plants growing in these habitats will be under greater threat in the future as invasive plants accelerate their spread, as woody encroachment increases, and as forest succession accelerates because of climate change. Alternative 2-Proposed Action Direct and Indirect Impacts There should be no adverse direct impacts to sensitive species located in floodplain and riparian forests, lakes ponds, creeks and other mesic areas if alternative 2 is chosen. Implementation of design criteria would ensure that sensitive plant species would be protected from harm if herbicide is used for non- native invasive plant control and/or treatment of woody encroachment. Infestations not analyzed in previous decisions would be reviewed by a botanist before herbicide treatment is implemented.

There should be beneficial indirect impacts to sensitive plants that grow in these habitat types. Implementation of the proposed action would help slow the rate at which invasive species are spreading across the Forest and could prevent many of them from reaching sensitive plants in these locations. The process to further authorize treatments of invasive plant infestations with herbicides would be greatly streamlined. It would be far easier to control species new to the Forest using EDRR, which should do much to prevent them from becoming widespread. Satellite infestations of existing infestations would be easier to treat in a timely manner. Rapid treatment of infestations at locations not currently authorized for treatment would be possible. Trees and shrubs threatening populations of sensitive plants could be treated more efficiently with herbicide at more sites. Cumulative Impacts Table 6 lists past, present, and reasonably foreseeable future actions, most of which affect the spread of non-native invasive plant s on the Shawnee National Forest. Adjacent agricultural lands that are farmed and grazed will continue to be sources of invasive infestations that spread into the Forest. Non- agricultural private residences will be a source, as well as new residential construction sites. Rights-of- way, such as roads and utility lines function as corridors for invasive species spread, as do system and non-system trails, and roads and driveways permitted for the use of private landowners. Visitor recreation, such as horseback riding, hiking, hunting, boating, kayaking, and illegal ATV use, will be a continuing source of invasive plant infestations. Wildfires will also affect the spread of invasives, the effects depending on the specific non-native invasive plant s present.

Forest management will continue to affect the spread of invasive plants, with some actions accelerating the spread and others decreasing it. Trail construction, firelines, and access paths for gully and shoreline stabilization will increase disturbed corridors that non-native invasive plants can invade and spread. Increased disturbance at active timber harvest sites will also increase sites where non-native invasive plant s are likely to invade and spread within the Forest. Maintenance of openlands using mowing and disking will also increase disturbance. On the other hand, integrated pest management will provide control of some invasive plant infestations. Prescribed fires, especially those taking place repeatedly at specific sites, will suppress several non-native invasive plant species. Herbicide, manual, and mechanical treatments of non-native invasive plant s have provided increased control of selected infestations across the Forest; future treatments will provide continued control.

The Shawnee National Forest has signed several decisions authorizing herbicide use (Table 7). Those decisions allow herbicide treatment on about 18% of the Shawnee National Forest. Increased herbicide treatment has already reduced the spread of many non-native invasive plant infestations on the Forest. Several projects authorized treatments to protect sensitive plants that grow at forested wetlands and swamps and to restore their habitats, not just through herbicide treatments, but also with tree and shrub removal and prescribed fire. Herbicide treatments have already reduced non-native invasive plant infestations at several sensitive plant locations. Future treatments should continue and expand to additional sites, restoring habitat and benefitting sensitive plants in more locations.

Implementation of the proposed action would have beneficial cumulative impacts to sensitive plant species found in floodplain and riparian forests, lakes ponds, creeks and other mesic areas. It would enhance and expand herbicide treatments across the Forest, not just 18% of it, slowing their spread and making it less likely that new infestations would reach sensitive plants growing in in these habitat types. Herbicide use could be expanded to locations where herbicide use to treat non-native invasive plant s and/or encroaching woody vegetation is not currently allowed. Along with prescribed fire, habitat at those sites would have a greater likelihood of being restored. Controlling non-native invasive plant s and woody encroachment with herbicide is more efficient and often more effective than manual and mechanical control, so habitat restoration could potentially take place at more sites on the Forest. Site damage would not be as great because fewer treatments would be needed. Sensitive plant populations growing in these habitats would be more likely to be preserved and may even increase in numbers. Therefore, implementation of the proposed project would have beneficial impacts to sensitive plants growing in floodplain and riparian forests, lakes ponds, creeks and other mesic areas. Open Barrens, Prairies, Glades, and Fields Current Condition and Expected Future Conditions Many populations of sensitive plants found in barrens, prairies, glades, and fields on the Forest are threatened by non-native invasive plants and/or by habitat degradation from woody encroachment. Several NEPA decisions (Invasive Species Management, Cretaceous Hills Ecological Restoration Project, and three prescribed burn projects) were signed that authorized management action to preserve them. Treatments allowed are—integrated pest management of non-native invasive plants, including herbicide treatments; control of encroaching woody vegetation, some sites with herbicide and others without it; and prescribed fire. Recently implemented treatments have shown promising results in reducing non- native invasive plant infestations near vulnerable plants and in improving their habitat. However, only about half of the sensitive plants populations found in the Forest’s barrens, prairies, glades, and fields are located at sites authorized for treatment under currently signed decisions.

Non-native invasive plant infestations can be treated at about half of the sensitive plant populations located in these types of habitats, but treatments may not be authorized for some non-native invasive plant species. If a non-native invasive plant that was not authorized for herbicide treatment becomes a threat, those infestations could not be treated with herbicides. EDRR treatments to control new species would be hampered with that restriction, making treatment less likely to be implemented and probably less effective if it does. Sensitive plants growing in these habitats types could potentially be threatened by these types of infestations.

24 extreme rainfall, flooding, drought, wildfires, and high winds will create habitat that invasive plants would be very likely to invade. All sensitive plants, including those growing in open barrens, prairies, glades and fields, would potentially be under greater threat from invasive plants in the future.

About a third of the known sites of sensitive plants found in barrens, prairies, glades, and fields on the Forest are authorized for treatments to control encroaching native woody vegetation with herbicide and about two thirds of those populations can be treated with prescribed fire. These plants require open canopy habitat and are being threatened by forest succession. Woody encroachment and forest succession are expected accelerate because of climate. Total rainfall expected to increase, allowing woody vegetation to spread more rapidly into open areas. Habitat for many of these sensitive plants is likely to shrink.

An example of a sensitive plant currently threatened by woody encroachment is white wand beardtongue (Penstemon tubaeflorus) at Ozark Hill Prairie Research Natural Area. This species reappeared at a hill prairie opening after the natural area was prescribed burned for the first time in decades. Trees at the site were then cut selectively to enlarge the prairie opening. However, when the site was monitored three years later following a second prescribed burn, its habitat was being overtaken by blackberry and sassafras. Those species were not being controlled by prescribed fire. Sassafras and blackberry resprout vigorously after cutting, requiring herbicide application to be adequately controlled. Unfortunately, herbicide use is not authorized at this natural area. Trying to control woody vegetation at this site by manually or mechanically cutting it would require repeated treatments that would increase trampling and could result in increased soil compaction.

To summarize, about half of the known sensitive plant populations found in barrens, prairies, glades, and fields on the Forest are located at sites where herbicide treatments are allowed. Treatments would continue to be implemented at those sites. However, the other half of those sensitive plant populations are in locations where herbicide use is not allowed. They remain under greater threat from non-native invasive plant infestations. Also, non-native invasive plant species not analyzed in most previous NEPA decisions could not be treated with herbicides, making EDRR control more difficult. These non-native invasive plant species may pose a threat to all sensitive plants growing in these habitats on the Forest. Control of encroaching woody vegetation may not be as effective at sites where herbicide use is not allowed; frequently repeated treatments may be necessary to effectively restore habitat for sensitive plants at those locations. The treatments themselves could damage the site because of soil compaction. Sensitive plants growing in these habitats are expected to become increasingly threatened in the future by non-native invasive plants, woody encroachment, and forest succession because of climate change.

Alternative 2-Proposed Action Direct and Indirect Impacts There should be no adverse direct impacts to sensitive species located in barrens, prairies, glades, and fields if alternative 2 is chosen. Implementation of design criteria would ensure that sensitive plant species would be protected from harm if herbicide is used for non-native invasive plant control and/or treatment of woody encroachment. Infestations not analyzed in previous decisions would be reviewed by a botanist before herbicide treatment is implemented.

25 across the Forest and could prevent many of them from reaching sensitive plants in these locations. The process to further authorize treatments of invasive plant infestations with herbicides would be greatly streamlined. It would be far easier to control species new to the Forest using EDRR, which should do much to prevent them from becoming widespread. Satellite infestations of existing infestations would be easier to treat in a timely manner. Rapid treatment of infestations at locations not currently authorized for treatment would be possible. Trees and shrubs threatening populations of sensitive plants could be treated more efficiently with herbicide at more sites. Cumulative Impacts Table 6 lists past, present, and reasonably foreseeable future actions, most of which affect the spread of non-native invasive plants on the Shawnee National Forest. Adjacent agricultural lands that are farmed and grazed will continue to be sources of invasive infestations that spread into the Forest. Non- agricultural private residences will be a source, as well as new residential construction sites. Rights-of- way, such as roads and utility lines function as corridors for invasive species spread, as do system and non-system trails, and roads and driveways permitted for the use of private landowners. Visitor recreation, such as horseback riding, hiking, hunting, and illegal ATV use, will be a continuing source of invasive plant infestations. Wildfires will also affect the spread of invasives, the effects depending on the specific non-native invasive plant species present.

Forest management will continue to affect the spread of invasive plants, with some actions accelerating the spread and others decreasing it. Trail construction, firelines, and access paths for gully and shoreline stabilization will increase disturbed corridors that invasive plants can invade and spread. Increased disturbance at active timber harvest sites will also increase sites where they are likely to invade and spread within the Forest. Maintenance of openlands using mowing and disking will also increase disturbance. On the other hand, integrated pest management will provide control of some invasive plant infestations. Prescribed fires, especially those taking place repeatedly at specific sites, will suppress several non-native invasive plant species. Herbicide, manual, and mechanical treatments of non-native invasive plants have provided increased control of selected infestations across the Forest; future treatments will provide continued control.

The Shawnee National Forest has signed several decisions authorizing herbicide use (Table 7). Those decisions allow herbicide treatment on about 18% of the Shawnee National Forest. Increased herbicide treatment has already reduced the spread of many infestations on the Forest. Several projects authorized treatments to protect sensitive plants that grow at barrens, prairies, glades, and fields and to restore their habitats, not just through herbicide treatments, but also with tree and shrub removal and prescribed fire. Herbicide treatments have already reduced non-native invasive plant infestations at several sensitive plant locations. Future treatments should continue and expand to additional sites, restoring habitat and benefitting sensitive plants in more locations.

Implementation of the proposed action would have beneficial cumulative impacts to sensitive plant species found in barrens, prairies, glades, and fields. It would enhance and expand herbicide treatments across the Forest, not just 18% of it, slowing their spread and making it less likely that new infestations would reach sensitive plants growing in in these habitat types. Herbicide use could be expanded to locations where herbicide use to treat non-native invasive plants is not currently allowed. Along with prescribed fire, habitat at those sites would have a greater likelihood of being restored. Controlling invasive plants with herbicide is more efficient and often more effective than manual and mechanical

26 control, so habitat restoration could potentially take place at more sites on the Forest. Site damage would not be as great because fewer treatments would be needed. Sensitive plant populations growing in these habitats would be more likely to be preserved and may even increase in numbers. Therefore, implementation of the proposed project would have beneficial impacts to sensitive plants growing in barrens, prairies, glades, and fields. Cliff Tops, Cliff Faces, Cliff Bases, and Rich Slopes of Cliffs Current Condition and Expected Future Conditions Many populations of sensitive plants found in cliff sites on the Forest are threatened by non-native invasive plants and/or by habitat degradation from shading due to woody encroachment. A number of NEPA decisions (Invasive Species Management, Cretaceous Hills Ecological Restoration Project, and several prescribed burn projects) were signed that authorized management action to preserve them. Treatments allowed are—integrated pest management of non-native invasive plants, including herbicide treatments; control of encroaching woody vegetation, some sites with herbicide and others without it; and prescribed fire. Recent prescribed fires have improved habitat for several of the sensitive plant species found in these habitats. However, less than half of the sensitive plants populations found in the Forest’s cliff areas are located at sites authorized for treatment under currently signed decisions.

Non-native invasive plant infestations can be herbicide treated at about 40% of the sensitive plant populations located in these types of habitats, leaving the rest vulnerable to this threat. Another potential threat is from non-native invasive plant species that have not been authorized for herbicide treatment at specific areas. If such non-native invasive plants become threats to sensitive plants, those infestations could not be treated with herbicides. EDRR to control new species would be hampered with that restriction, making treatments less likely to be implemented and probably less effective if they take place. Most sensitive plant populations growing in cliff habitats on the Forest would remain vulnerable to competition from non-native invasive plant infestations.

Threats from non-native invasive plants are likely to increase in the future. The spread of invasive plants is expected to accelerate, in large part due to climate change. Increased disturbance and erosion from extreme rainfall, flooding, drought, wildfires, and high winds will create habitat that invasive plants would be very likely to invade. All sensitive plants, including those growing in and around cliffs, would potentially be under greater threat from invasive plants in the future.

About a third of the known sites of sensitive plants found in cliff areas on the Forest are authorized for treatments to control encroaching native woody vegetation with herbicide, and about two thirds of those populations can be treated with prescribed fire. Many of these plants require open canopy habitat and are being threatened by forest succession, while others thrive at shaded sites and are increasing their populations in southern Illinois. Forest succession is expected to accelerate as increased rainfall from climate change would favor the growth of woody vegetation. Open canopy habitat is likely to shrink even more rapidly than it is already, threatening several species that grow in cliff habitats.

Prescribed fire has improved habitat for some sensitive plant species, such as the Carolina thistle at Cave Hill Research Natural Area. However, some populations are threatened by shading from woody vegetation that has not been reduced despite several rounds of prescribed fire. These locations would benefit from tree and/or shrub removal, but herbicide use is not allowed at most. Manual removal of

27 woody vegetation at cliff sites can be especially difficult because the thin soils can easily be pulled away, which would degrade habitat for many sensitive plants at cliff sites.

Limber honeysuckle and yellow honeysuckle are examples of species that are being threatened by non- native invasive plants and by shading. Both species are present at the Little Grand Canyon/Horseshoe Bluff Ecological Area, where they grow on sandstone ledges and bluffs. Sites where these woody vines are found have been invaded by Japanese honeysuckle. No treatments to improve habitat are authorized at this natural area, including herbicide treatments. Hand-pulling infestations is not an option since it would pull away the thin soils at cliff sites where limber and yellow honeysuckle grow. Both species grow best at lightly shaded sites. Forest succession due to lack of fire has resulted in heavy shading at most cliff sites in this natural area. Excessive shade is likely the reason that most of the rare honeysuckle plants seen there in the last two decades have been sterile; plants are not receiving sufficient light to flower.

To summarize, less than half of the known sensitive plant populations found at cliff tops, cliff faces, cliff bases, and rich slopes of cliffs on the Forest are located at sites where herbicide treatments are allowed. Treatments would continue to be implemented at authorized sites. However, the rest of those sensitive plant populations will remain under greater threat from non-native invasive plant infestations and/or woody encroachment. Using manual methods to remove non-native invasive plants or trees and shrubs at cliff sites is often not an option, since treatments can result in removing fragile soils in which the sensitive plants are growing. EDRR control to control new non-native invasive plant species would be difficult without being able to use herbicide. These non-native invasive plants could pose a threat to all sensitive plant species growing in these habitats, and that threat is likely to increase in the future because of accelerated spread due to climate change. Climate change is also likely to increase woody encroachment and forest succession in the future, which would pose a threat to several of the sensitive species on the Forest that grow in these habitats. Alternative 2-Proposed Action Direct and Indirect Impacts There should be no adverse direct impacts to sensitive species located cliff habitats if alternative 2 is chosen. Implementation of design criteria would ensure that sensitive plant species would be protected from harm if herbicide is used for non-native invasive plant control and/or treatment of woody encroachment. Infestations not analyzed in previous decisions would be reviewed by a botanist before herbicide treatment is implemented.

Cumulative Impacts Table 6 lists past, present, and reasonably foreseeable future actions, most of which affect the spread of non-native invasive plants on the Shawnee National Forest. Adjacent agricultural lands that are farmed and grazed will continue to be sources of invasive infestations that spread into the Forest. Non- agricultural private residences will be a source, as well as new residential construction sites. Rights-of- way, such as roads and utility lines function as corridors for invasive species spread, as do system and non-system trails, and roads and driveways permitted for the use of private landowners. Visitor recreation, such as horseback riding, hiking, hunting, and illegal ATV use, will be a continuing source of invasive plant infestations. Wildfires will also affect the spread of invasives, the effects depending on the specific non-native invasive plant species present.

Forest management will continue to affect the spread of invasive plants, with some actions accelerating the spread and others decreasing it. Trail construction, firelines, and access paths for gully and shoreline stabilization will increase disturbed corridors that invasive plants can invade and spread. Increased disturbance at active timber harvest sites will also increase sites where they are likely to invade and spread within the Forest. Maintenance of openlands using mowing and disking will also increase disturbance. On the other hand, integrated pest management will provide control of some invasive plant infestations. Prescribed fires, especially those taking place repeatedly at specific sites, will suppress several non-native invasive plant species. Herbicide, manual, and mechanical treatments of non-native invasive plants have provided increased control of selected infestations across the Forest; future treatments will provide continued control.

The Shawnee National Forest has signed several decisions authorizing herbicide use (Table 7). Those decisions allow herbicide treatment on about 18% of the Shawnee National Forest. Increased herbicide treatment has already reduced the spread of many infestations on the Forest. Several projects authorized treatments to protect sensitive plants that grow at cliff habitats and to restore their habitats, not just through herbicide treatments, but also with manual tree and shrub removal and prescribed fire. Herbicide treatments have not yet been used to protect sensitive plant populations at cliff sites, although it is currently authorized at a several sites. Treatments should take place in the future, restoring habitat and benefitting more sensitive plant populations.

Implementation of the proposed action would have beneficial cumulative impacts to sensitive plant species found in cliff habitats. It would enhance and expand herbicide treatments across the Forest, not just 18% of it, slowing their spread and making it less likely that new infestations would reach sensitive plants growing in in these habitat types. Herbicide use could be expanded to locations where herbicide use to treat non-native invasive plants and woody encroachment is not currently allowed. Along with prescribed fire, habitat at those sites would have a greater likelihood of being restored. Controlling invasive plants and woody vegetation with herbicide is more efficient and often more effective than manual and mechanical control, so habitat restoration could potentially take place at more sites on the Forest. Site damage would not be as great because there would be far less disturbance and fewer treatments would be needed. Sensitive plant populations growing in these habitats would be more likely to be preserved and may even increase in numbers. Therefore, implementation of the proposed project would have beneficial impacts to sensitive plants growing in cliff habitats.

Xeric, Dry, and Dry-Mesic Upland Woods, and Pine Plantations Current Condition and Expected Future Conditions Many populations of sensitive plants found in xeric, dry, and dry-mesic upland woods, and pine plantations on the Forest are threatened by non-native invasive plants and/or by habitat degradation from shading due to woody encroachment and forest mesophication. A number of NEPA decisions (Invasive Species Management, Cretaceous Hills Ecological Restoration Project, Waterfall Stewardship Piot Project, and several prescribed burn projects) were signed that authorized management actions that would help to preserve them. Treatments allowed are—integrated pest management of non-native invasive plants, including herbicide treatments; control of encroaching woody vegetation, some sites with herbicide and others without it; stand improvement with and without herbicide; and prescribed fire. Recent prescribed fires have improved habitat for several of the sensitive plant species found in these habitats. However, less than a third of the sensitive plants populations found in the Forest’s xeric, dry, and dry-mesic upland woods, and pine plantations are located at sites authorized for any of these treatments under currently signed decisions.

Non-native invasive plant infestations can be herbicide treated at about a quarter of the sensitive plant populations located in these types of habitats, leaving the rest vulnerable to this threat. Another potential threat is from non-native invasive plant species that have not been authorized for herbicide treatment at specific areas. If such non-native invasive plants become threats to sensitive plants, those infestations could not be treated with herbicides. EDRR to control new species would be hampered with that restriction, making treatments less likely to be implemented and probably less effective if they take place. Most sensitive plant populations growing in the drier woodlands and pine plantations on the Forest would remain vulnerable to competition from non-native invasive plant infestations.

Less than 10% of the known sites of sensitive plants found in xeric, dry, and dry-mesic upland woods, and pine plantations on the Forest are authorized for treatments to control encroaching native woody vegetation with herbicide, and about a third of those populations can be treated with prescribed fire. Many of these plants require open canopy habitat and are being threatened by forest succession. Several thrive at shaded, but not heavily shaded, sites, and are being threatened by forest mesophication. Prescribed fire has improved habitat for some of those sensitive plant species by suppressing native shade-tolerant trees, allowing restoration of oak-hickory woodlands. One example of fire’s success in habitat restoration is for the chestnut oak at Atwood Ridge Research Natural Area. However, many populations are threatened by shading from woody vegetation because their locations cannot be treated by herbicide or by prescribed fire. Manual control methods alone cause more disturbance and would be less effective; resprouting vegetation would require repeated treatments and result in repeated trampling that could cause soil compaction.

The spiked crested coralroot at the Whoopie Cat Mountain natural areas is an example of a sensitive plant growing in xeric woodlands that is threatened by woody encroachment from invasive shrubs. This orchid grows in dry, sunny to lightly shaded habitats where competing vegetation is minimal. The glades and surrounding woodlands where spiked crested coralroot have been found are becoming increasingly dominated by the non-native shrubs autumn olive (Elaeagnus umbellata) and Amur honeysuckle (Lonicera maackii). The open canopy at Whoopie Cat Mountain is gradually disappearing, threatening crested coralroot with possible extirpation. These shrubs cannot be effectively controlled by cutting alone because they resprout vigorously. Herbicide treatments, either foliar or cut stump, has been

30 shown to be effective in killing them, but herbicide use is not authorized at this site. Prescribed fire and manually cutting woody vegetation are authorized there and can suppress autumn olive and Amur honeysuckle to some extent. However, burning alone is not as effective at controlling invasive shrubs as is using herbicides. Continued habitat degradation is a threat to the spiked crested coralroot occurrences at these natural areas.

Threats to sensitive plant populations at xeric, dry, and dry-mesic upland woods are likely to increase in the future. Forest mesophication and the spread of invasive plants are expected to accelerate, in large part due to climate change. Total rainfall should increase, favoring shade tolerant trees and an expansion of mesic forests at the expense of drier upland forests and woodlands. Although timber harvests, stand improvement, and prescribed fire would slow mesophication, stand improvement to reduce shade tolerant trees would not be as effective without herbicide use. Increased disturbance and erosion from extreme rainfall, flooding, drought, wildfires, and high winds will create habitat that invasive plants would be very likely to invade. All sensitive plants would potentially be under greater threat from invasive plants in the future, and sensitive plant species that grow in drier forest and woodlands would be under threat from shrinking habitat resulting from forest mesophication.

To summarize, less than 10% of the known sensitive plant populations found at xeric, dry, and dry-mesic upland woods, and pine plantations on the Forest are located at sites where herbicide treatments are allowed. Treatments would continue to be implemented at authorized sites. However, the rest of those sensitive plant populations will remain under greater threat from non-native invasive plant infestations, woody encroachment, and forest mesophication, especially in the future due to climate change. Using manual methods to remove non-native invasive plants or trees and shrubs is less efficient and effective than using herbicide, limiting the number of sites where treatments can take place to protect these sensitive plants and their habitats. Manual control of woody vegetation often requires more treatments, increasing disturbance and soil compaction, which could degrade sensitive plant habitat. Using EDRR to control new non-native invasive plant species would difficult without being able to use herbicide. These types of non-native invasive plants could pose a threat to all sensitive plant species growing in these habitats on the Forest. Prescribed burning and stand improvement without the use of herbicide may be insufficient to effectively restore habitat at xeric, dry, and dry to mesic upland wood habitats where these sensitive plants are found.

Alternative 2-Proposed Action Direct and Indirect Impacts There should be no adverse direct impacts to sensitive species located at xeric, dry, and dry-mesic upland woods, and pine plantations if alternative 2 is chosen. Implementation of design criteria would ensure that sensitive plant species would be protected from harm if herbicide is used for non-native invasive plant control and/or treatment of woody encroachment. Infestations not analyzed in previous decisions would be reviewed by a botanist before herbicide treatment is implemented.

31 much to prevent them from becoming widespread. Satellite infestations of existing infestations would be easier to treat in a timely manner. Rapid treatment of infestations at locations not currently authorized for treatment would be possible. Trees and shrubs threatening populations of sensitive plants could be treated more efficiently with herbicide at more sites, and treatments would cause far less damage than manual methods. Herbicide could be used for stand improvement to reduce shade- tolerant native trees and improve habitat for these plant species. Cumulative Impacts Table 6 lists past, present, and reasonably foreseeable future actions, most of which affect the spread of non-native invasive plants on the Shawnee National Forest. Adjacent agricultural lands that are farmed and grazed will continue to be sources of invasive infestations that spread into the Forest. Non- agricultural private residences will be a source, as well as new residential construction sites. Rights-of- way, such as roads and utility lines function as corridors for invasive species spread, as do system and non-system trails, and roads and driveways permitted for the use of private landowners. Visitor recreation, such as horseback riding, hiking, hunting, and illegal ATV use, will be a continuing source of invasive plant infestations. Wildfires will also affect the spread of invasives, the effects depending on the specific non-native invasive plant species present.

Forest management will continue to affect the spread of invasive plants, with some actions accelerating the spread and others decreasing it. Trail construction, firelines, and access paths for gully and shoreline stabilization will increase disturbed corridors that invasive plants can invade and spread. Increased disturbance at active timber harvest sites will also increase sites where they are likely to invade and spread within the Forest. Maintenance of openlands using mowing and disking will also increase disturbance. On the other hand, integrated pest management will provide control of some invasive plant infestations. Prescribed fires, especially those taking place repeatedly at specific sites, will suppress several non-native invasive plant species. Herbicide, manual, and mechanical treatments of non-native invasive plants have provided increased control of selected infestations across the Forest; future treatments will provide continued control.

The Shawnee National Forest has signed several decisions authorizing herbicide use (Table 7). Those decisions allow herbicide treatment on about 18% of the Shawnee National Forest. Increased herbicide treatment has already reduced the spread of many infestations on the Forest. Several projects authorized treatments that would protect these sensitive plant species and to restore their habitats, not just through herbicide treatments, but also with manual tree and shrub removal, prescribed fire, and stand improvement to reduced shade-tolerant native trees. Herbicide treatments have only been used to protect sensitive plant populations at a few xeric, dry, and dry-mesic upland woods locations, although it is currently authorized at a several sites. More treatments should take place in the future, restoring habitat and benefitting more sensitive plant populations.

Implementation of the proposed action would have beneficial cumulative impacts to sensitive plant species found in xeric, dry, and dry-mesic upland woods, and pine plantations. It would enhance and expand herbicide treatments across the Forest, not just 18% of it, slowing their spread and making it less likely that new infestations would reach sensitive plants growing in in these habitat types. Herbicide use could be expanded to locations where herbicide use to treat non-native invasive plants and woody encroachment is not currently allowed. Along with prescribed fire, habitat at those sites would have a greater likelihood of being restored. Controlling invasive plants and woody vegetation with herbicide is

32 more efficient and often more effective than manual and mechanical control, so habitat restoration could potentially take place at more sites on the Forest. Site damage would not be as great because there would be far less disturbance and fewer treatments would be needed. Using herbicide in stand improvements to reduce forest mesophication and restore oak hickory woodlands would allow the improvement of more habitat for these species. Sensitive plant populations growing in these habitats would be more likely to be preserved and may even increase in numbers. Therefore, implementation of the proposed project would have beneficial impacts to sensitive plants growing in xeric, dry, and dry- mesic upland woods, and pine plantations. Dry-Mesic and Mesic Upland Woods, Hollows, and Ravines Current Condition and Expected Future Conditions Many populations of sensitive plants found in dry-mesic and mesic upland woods, hollows, and ravines on the Forest are threatened by non-native invasive plants, and some are threatened by habitat degradation from shading due to woody encroachment. A number of NEPA decisions (Invasive Species Management, Phragmites and Reed Canarygrass Management, Waterfall Stewardship Pilot Project, and several prescribed burn projects) were signed that authorized management actions that would help to preserve them. Treatments allowed are—integrated pest management of non-native invasive plants, including herbicide treatments; control of encroaching woody vegetation, some sites with herbicide and others without it; stand improvement, with and without the use of herbicides; and prescribed fire. Recent prescribed fires have improved habitat for a few of the sensitive plant species found in these habitats. However, most of the sensitive plant populations found in these habitats on the Forest are not located at sites authorized for any of these treatments under currently signed decisions.

Non-native invasive plant infestations can be herbicide treated at only a few of the sensitive plant populations located in these types of habitats, leaving the rest vulnerable to this threat. Another potential threat is from non-native invasive plant species that have not been authorized for herbicide treatment at specific areas. If such non-native invasive plants become threats to sensitive plants, those infestations could not be treated with herbicides. EDRR to control new species would be hampered with that restriction, making treatments less likely to be implemented and probably less effective if they take place. Most sensitive plant populations growing in mesic and dry-mesic woodlands on the Forest would remain vulnerable to competition from non-native invasive plant infestations.

Only a few of the known sites of sensitive plants found in dry-mesic and mesic upland woods, hollows, and ravines on the Forest are authorized for treatments to control encroaching native woody vegetation with herbicide, and about a third of those populations can be treated with prescribed fire. Although about half of these plants grow best under deep shade in rich woods, the rest grow better in lightly shaded to partially open canopy habitats and are being threatened by forest succession. Prescribed fire has improved habitat for some of these sensitive plant species, such as the goldenseal in the Kinkaid Lake vicinity. However, many populations are threatened by shading from woody vegetation or from forest mesophication due to the expansion of shade tolerant trees. Most locations cannot be treated by herbicide or by prescribed fire. Manual control methods alone cause more disturbance and would be less effective; resprouting vegetation would require repeated treatments and result in repeated trampling that could cause soil compaction.

The bigleaf snowbell growing at the Wolf Creek Botanical Area is an example of a sensitive plant that is threatened by forest succession and from non-native invasive shrubs. This small tree grows in dry-mesic

33 upland forests. The site where this population is located has become so heavily shaded that the trees rarely flower, and reproduction is mainly vegetative. Fortunately, prescribed fire is authorized at this natural area and has recently taken place there after an absence of several decades. Future burns could reduce heavy shade there. The bigleaf snowbell trees at this natural area are also threatened by nearby infestations of autumn olive and Amur honeysuckle. The infestations will eventually spread to the bigleaf snowbell trees if they are not stopped. These shrubs cannot be effectively controlled by cutting alone because they resprout vigorously. Herbicide treatments, either foliar or cut stump, has been shown to be effective in killing them, but herbicide use is not authorized at this site. Prescribed fire and manually cutting woody vegetation are allowed and can suppress autumn olive and Amur honeysuckle to some extent. However, it is not as effective a control as herbicide treatments.

Threats to sensitive plant populations found in these habitats are likely to increase in the future. Forest mesophication and the spread of invasive plants are expected to accelerate in the future, in large part due to climate change. Total rainfall should increase, favoring shade tolerant trees and an expansion of mesic forests at the expense of drier upland forests and woodlands. Although timber harvests, stand improvement, and prescribed fire would slow mesophication, stand improvement to reduce shade tolerant trees would not be as effective without herbicide use. Increased disturbance and erosion from extreme rainfall, flooding, drought, wildfires, and high winds will create habitat that invasive plants would be very likely to invade. All sensitive plants would potentially be under threat from invasive plants in the future, and sensitive plant species that grow in drier forest and woodlands would be under threat from shrinking habitat resulting from forest mesophication. To summarize, few of the known sensitive plant populations found dry-mesic and mesic upland woods, hollows, and ravines on the Forest are located at sites where herbicide treatments are allowed. Treatments would continue to be implemented at authorized sites. However, the rest of those sensitive plant populations will remain under greater threat from non-native invasive plant infestations, woody encroachment, and forest succession. These threats are only expected to increase in the future because of climate change. Using manual methods to remove non-native invasive plants, encroaching trees and shrubs, or shade tolerant woody vegetation is less efficient and effective than using herbicide, limiting the sites where treatments can take place to protect these sensitive plants and their habitats. Manual control of woody vegetation often requires more treatments, increasing disturbance and soil compaction, which could degrade sensitive plant habitat. Using EDRR to control new non-native invasive plant species would be difficult without being able to use herbicide. These types of non-native invasive plants could pose a threat to all sensitive plant species growing in these habitats on the Forest.

Alternative 2-Proposed Action Direct and Indirect Impacts There should be no adverse direct impacts to sensitive plants located at dry-mesic and mesic upland woods, hollows, and ravines if alternative 2 is chosen. Implementation of design criteria would ensure that sensitive plant species would be protected from harm if herbicide is used for non-native invasive plant control and/or treatment of woody encroachment. Infestations not analyzed in previous decisions would be reviewed by a botanist before herbicide treatment is implemented.

34 process to further authorize treatments of invasive plant infestations with herbicides would be greatly streamlined. It would be far easier to control species new to the Forest using EDRR, which should do much to prevent them from becoming widespread. Satellite infestations of existing infestations would be easier to treat in a timely manner. Rapid treatment of infestations at locations not currently authorized for treatment would be possible. Trees and shrubs threatening populations of sensitive plants and shade tolerant woody vegetation causing forest mesophication could be treated more efficiently with herbicide at more sites, and treatments would cause far less damage than manual methods.

Forest management will continue to affect the spread of invasive plants, with some actions accelerating the spread and others decreasing it. Trail construction, firelines, and access paths for gully and shoreline stabilization will increase disturbed corridors that invasive plants can invade and spread. Increased disturbance at active timber harvest sites will also increase sites where they are likely to invade and spread within the Forest. Maintenance of openlands using mowing and disking will also increase disturbance. On the other hand, integrated pest management will provide control of some invasive plant infestations. Prescribed fires, especially those taking place repeatedly at specific sites, will suppress several non-native invasive plant species. Herbicide, manual, and mechanical treatments of non-native invasive plants have provided increased control of selected infestations across the Forest; future treatments will provide continued control.

The Shawnee National Forest has signed several decisions authorizing herbicide use (Table 7). Those decisions allow herbicide treatment on about 18% of the Shawnee National Forest. Increased herbicide treatment has already reduced the spread of many infestations on the Forest. Several projects authorized treatments that would protect these sensitive plant species and restore their habitats, not just through herbicide treatments, but also with manual tree and shrub removal, stand improvement, and prescribed fire. Herbicide treatments have only been used to protect sensitive plant populations at a few dry-mesic and mesic upland woods locations, although it is currently authorized at a several sites. More treatments should take place in the future, restoring habitat and benefitting more sensitive plant populations.

Implementation of the proposed action would have beneficial cumulative impacts to sensitive plant species found in dry-mesic and mesic upland woods, hollows, and ravines. It would enhance and expand herbicide treatments across the Forest, not just 18% of it, slowing their spread and making it less likely that new infestations would reach sensitive plants growing in in these habitat types. Herbicide use could be expanded to locations where herbicide use to treat non-native invasive plants and woody

35 encroachment is not currently allowed. Herbicide use would improve the efficiency of stand improvement treatments to reduce forest mesophication. Along with prescribed fire, habitat at those sites would have a greater likelihood of being restored. Controlling invasive plants, encroaching trees and shrubs, and shade tolerant woody vegetation with herbicide is more efficient and often more effective than manual and mechanical control, so habitat restoration could potentially take place at more sites on the Forest. Site damage would not be as great because there would be far less disturbance and fewer treatments would be needed. Sensitive plant populations growing in these habitats would be more likely to be preserved and may even increase in numbers. Therefore, implementation of the proposed project would have beneficial impacts to sensitive plants growing in dry-mesic and mesic upland woods, hollows, and ravines.

Summary of Impacts to RFSS Plants Current Condition and Expected Future Conditions Many populations of sensitive plants on the Shawnee National Forest are at risk. Major threats are non- native invasive plant infestations, habitat degradation from non-native invasive plants and/or from woody encroachment, and forest mesophication. Several decisions have been signed authorizing management action to preserve some of the most vulnerable sensitive plant species and their habitats. Treatments include integrated pest management of non-native invasive plants, including herbicide treatments; removal of encroaching woody vegetation, some sites with herbicide and others without it; stand improvement to remove shade tolerant woody vegetation; selected timber harvests; and prescribed fire. Recently implemented treatments at several sensitive plant sites have shown promising results in reducing non-native invasive plant infestations and in improving their habitat. Some sensitive plant occurrences have increased in numbers following prescribed fire and herbicide control of non- native invasive plant infestations. Those treatments would continue to take place.

However, most sensitive plant sites on the Forest are not covered by those decisions and are still at risk. Treatments authorized by project decisions continue to be implemented, but the use of herbicides to preserve sensitive plant populations remains limited. Herbicide treatments, often the most effective and efficient control method for non-native invasive plants and woody vegetation, are allowed on only about 18% of the Forest’s lands (see Table 2). Herbicides cannot be used to treat non-native invasive plant infestations across most of the Forest, including most sensitive plant sites. Most newly discovered non-native plant species on the Forest cannot be effectively treated in a timely manner to prevent their spread. Implementing manual and mechanical methods to control infestations can sometimes cause such severe disturbance to sensitive plant sites that the treatments themselves threaten those plants. Manual and mechanical treatments require more manpower than herbicide application, and often require more treatments than herbicide. Using those methods is not always a practical option. Control of shrubs and other woody vegetation threatening sensitive plant habitat continues to be problematic since many species re-sprout vigorously despite repeated cutting and prescribed fire. Relatively few sensitive plant sites on the Forest are authorized for woody vegetation control with herbicides, making habitat restoration less efficient than it could be if herbicide use were allowed.

Threats to sensitive plant populations and their habitats are likely to increase in the future. Forest mesophication and the spread of invasive plants are expected to accelerate in the future, in large part due to climate change. Total rainfall should increase, favoring shade tolerant trees and an expansion of

36 mesic forests at the expense of drier upland forests and woodlands. Although timber harvests, stand improvement, and prescribed fire would slow mesophication, stand improvement to reduce shade tolerant trees would not be as effective without herbicide use. Increased disturbance and erosion from extreme rainfall, flooding, drought, wildfires, and high winds will created habitat that invasive plants would be very likely to invade. All sensitive plants would potentially be under threat from invasive plants in the future, and sensitive plant species that grow in drier forest and woodlands would be under threat from shrinking habitat resulting from forest mesophication.

The number of sensitive plant populations threatened by woody encroachment is also expected to grow. Herbicide use to control woody encroachment is not allowed at most sites. Control using only manual or mechanical methods is often more difficult, less effective, and causes more disturbance. Many woody species resprout without herbicide treatment, so sites would have to be treated again and again. With limited funding and personnel, fewer sites are likely to be treated. This would cause habitat degradation for many sensitive plants, especially for species growing in open canopy habitats such as clifftops, barrens, glades, and hill prairies. Increased disturbance at those sites could also increase the likelihood of invasive plant infestations.

Alternative 2-Proposed Action Direct and Indirect Impacts There should be no adverse direct impacts to sensitive species on the Forest if alternative 2 is chosen. Implementation of design criteria would ensure that sensitive plant species would be protected from harm if herbicide is used for non-native invasive plant control and/or treatment of woody encroachment. Infestations not analyzed in previous decisions would be reviewed by a botanist before herbicide treatment is implemented.

There should be beneficial indirect impacts to sensitive plants if alternative 2 is chosen. Implementation of the proposed action would help slow the rate at which invasive species are spreading across the Forest and could prevent many of them from reaching sensitive plants and their surrounding habitats. The process to authorize treatments of invasive plant infestations with herbicides would be greatly streamlined. Rapid treatment of infestations wherever necessary would be possible. Satellite infestations of existing infestations would be easier to treat in a timely manner. It would be far easier to control species new to the Forest using EDRR, which should do much to prevent them from becoming widespread. Trees and shrubs threatening populations of sensitive plants could be treated more efficiently with herbicide at more locations. Stand improvement using herbicide would also be more efficient and would help prevent mesophication of upland oak-hickory forests, which would improve habitat at many sensitive plant locations. Cumulative Impacts Table 6 lists past, present, and reasonably foreseeable future actions, most of which affect the spread of non-native invasive plants on the Shawnee National Forest. Adjacent agricultural lands that are farmed and grazed will continue to be sources of invasive infestations that spread into the Forest. Non- agricultural private residences will be another source, as well as new residential construction sites. Rights-of-way, such as roads and utility lines will continue to function as corridors for invasive species spread, as will system and non-system trails, and roads and driveways permitted for the use of private landowners. Visitor recreation, such as horseback riding, hiking, hunting, boating, kayaking, and illegal

ATV use, will be a continuing source of invasive plant infestations. Wildfires will also affect the spread of invasives, the effects depending on the specific invasive plants present.

Forest management will continue to affect the spread of invasive plants, with some actions accelerating the spread and others decreasing it. Trail construction, firelines, and access paths for gully and shoreline stabilization will increase disturbed corridors that non-native invasive plants can invade and spread. Increased disturbance at active timber harvest sites will increase sites where non-native invasive plants are likely to invade and spread within the Forest. Maintenance of openlands using mowing and disking will also increase disturbance. On the other hand, integrated pest management will provide control of some invasive plant infestations. Prescribed fires, especially those taking place repeatedly at specific sites, will suppress several non-native invasive plant species. Herbicide, manual, and mechanical treatments of non-native invasive plants have provided increased control of selected infestations across the Forest; future treatments will provide continued control.

The Shawnee National Forest has signed several decisions authorizing herbicide use (Table 7). Those decisions allowed herbicide treatment on about 18% of the Shawnee National Forest. Increased herbicide treatments have already reduced the spread of many non-native invasive plant infestations on the Forest. Several projects authorized treatments to protect some of the most threatened sensitive plant species and to restore their habitats through herbicide treatments, as well as with tree and shrub removal and prescribed fire. Herbicide treatments have already reduced non-native invasive plant infestations at several sensitive plant locations. Future treatments should continue and expand to additional sites, restoring habitat and benefitting sensitive plants in more locations.

Implementation of the proposed action would have beneficial cumulative impacts to sensitive plant species. It would enhance and expand herbicide treatments across the Forest, not just 18% of it, slowing the spread of non-native invasive plants and making it less likely that new infestations would reach sensitive plant populations. Herbicide use could be expanded to sensitive plant sites where herbicide use to treat non-native plant infestations and/or encroaching woody vegetation is not currently allowed. Along with prescribed fire, habitat at those sites would have a greater likelihood of being restored. Controlling non-native invasive plants and woody encroachment with herbicide is more efficient and often more effective than manual and mechanical control, so habitat restoration could potentially take place at more sites on the Forest. More efficient stand improvement from using herbicides would enhance restorations at oak-hickory forests and woodlands and would also expand the number of sensitive plant sites that could be treated. Sensitive plant populations growing in treated habitats would be more likely to be preserved and may even increase in numbers. Therefore, implementation of the proposed project would have beneficial impacts to sensitive plants on the Shawnee National Forest.

/s/Elizabeth Longo Elizabeth Longo, on March 14, 2019 Botanist, Shawnee National Forest

Revised by /s/Shannan Sharp Shannan Sharp on April 27, 2020 Botanist, Shawnee National Forest

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NatureServe. 2019. NatureServe Explorer: An online encyclopedia of life [web application]. Version 7.1. NatureServe, Arlington, Virginia. Available Link to http://www.natureserve.org/explorer. (Accessed March 14, 2019).

Nÿboer, R., and J.E. Ebinger. 2004. Endangered and Threatened Species of Illinois: Status and Distribution, Volume 3: 2004 Changes to the Illinois List of Endangered and Threatened Plant Species. Published by the Illinois Endangered Species Protection Board. 34 pp.

Phillippe, L.R. 2004a. Unreviewed Draft Conservation Assessment for Chelone obliqua Linnaeus var. speciosa Pennell & Wherry). Provided to the USDA Forest Service, Shawnee and Hoosier National Forests December 16, 2004 (dated 2004). Illinois Natural History Survey, Center for Biodiversity, 607 East Peabody Drive, Champaign, Ill. 8 pp.

Phillippe, L.R. 2004b. Unreviewed Draft Conservation Assessment for Eleocharis wolfii (A. Gray). Provided to the USDA Forest Service, Shawnee and Hoosier National Forests December 16, 2004 (dated 2004). Illinois Natural History Survey, Center for Biodiversity, 607 East Peabody Drive, Champaign, Ill. 10 pp.

Phillippe, L.R. 2004c. Unreviewed Draft Conservation Assessment for Phaeophyscia leana (Tuckerman) Esslinger. Provided to the USDA Forest Service, Shawnee and Hoosier National Forests December 16, 2004 (dated 2004). Illinois Natural History Survey, Center for Biodiversity, 607 East Peabody Drive, Champaign, Ill. 24 pp.

Phillippe, L.R. 2004d. Unreviewed Draft Conservation Assessment for Stenanthium gramineum (Ker Gawler) Morang. Provided to the USDA Forest Service, Shawnee and Hoosier National Forests December 16, 2004 (dated 2004). Illinois Natural History Survey, Center for Biodiversity, 607 East Peabody Drive, Champaign, Ill. 128 pp.

Ramstetter, Jennifer M. 2001. Unreviewed Draft Conservation Assessment for Threebirds Orchid (Triphora trianthophora). Prepared for the Eastern Region of the Forest Service, Threatened and Endangered Species Program, Milwaukee, Wisconsin, 76 pp.

Schwegman, J. 1969. Vegetation of some seep springs in the Cretaceous Hills of southern Illinois. A thesis submitted in partial fulfillment of the requirements for the degree of Master of Arts. Department of Botany, Southern Illinois University, Carbondale. 81 pp.

Schultz, Jan. 2003. Conservation Assessment for Butternut or White Walnut (Juglans cinerea) L. Hiawatha National Forest. Gladstone, MI. 76 pp.

Schwegman, J. 1982. A new species of Oxalis. Phytologia 50(7):463-467.

Schwegman, J. 1999. A survey to determine the status of Filmy Fern (Trichomanes boschianum) sporophyte populations formerly known or reported from Illinois. Report by John E. Schwegman on April 15, 1999 to the Forest Service. 36 pages including maps.

Schwegman, J. 2001. Email to Elizabeth Shimp regarding Buchnera americana dated April 5, 2001. 1 page.

Taft, J.B. 2004a. Unreviewed Draft Conservation Assessment for Amorpha nitens Boynton. Provided to the USDA Forest Service, Shawnee and Hoosier National Forests December 15, 2004. Illinois Natural History Survey, Center for Biodiversity, 607 East Peabody Drive, Champaign, Ill. 21 pp.

Taft, J.B. 2004b. Unreviewed Draft Conservation Assessment for Trifolium reflexum L. Provided to the USDA Forest Service, Shawnee and Hoosier National Forests December 15, 2004. Illinois Natural History Survey, Center for Biodiversity, 607 East Peabody Drive, Champaign, Ill. 19 pp.

Taft, J.B. 2005. Conservation Assessment for Platanthera flava (L.) Lindl. var. flava. Technical Report 2005 (8). Prepared for Eastern Region of the Forest Service Threatened and Endangered Species Program. Milwaukee, Wisconsin. 35 pp.

Tucker, Gordon C., and John E. Ebinger. 2011. A Review of the Genus Scleria (Cyperaceae) in Illinois. Transactions of the Illinois State Academy of Science. Vol. 104: 3-4, pp. 109-118.

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USDA, NRCS. 2018. The PLANTS Database, (http://plants.usda.gov). National Plant Data Center, Baton Rouge, LA 70874-4490 USA.

USDA, NRCS. 2019. The PLANTS Database, (http://plants.usda.gov). National Plant Data Center, Baton Rouge, LA 70874-4490 USA.

USDA, NRCS. 2020. The PLANTS Database, (http://plants.usda.gov). National Plant Data Center, Baton Rouge, LA 70874-4490 USA.

USDA FS. 2005. Shawnee National Forest Biological Evaluation for Regional Forester’s Sensitive Plant Species, Forest Plan Revision. Shawnee National Forest, Harrisburg, Illinois. 116 pp. Accessed at: http://www.fs.usda.gov/Internet/FSE_DOCUMENTS/stelprdb5151585.pdf

USDA FS. 2006. Land and Resource Management Plan, Shawnee National Forest. Harrisburg, Illinois.

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USDA Forest Service Manual 2672.

USDA Forest Service Manual 2670-2671.

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Yatskievych, G. 1999. Steyermark's Flora of Missouri: Volume 1. Published by Missouri Department of Conservation in cooperation with Missouri Botanic Garden Press, St. Louis, Missouri. 991 pp.

Yatskievych, George. 2006. Steyermark's Flora of Missouri: Volume 2. Published by Missouri Department of Conservation in cooperation with Missouri Botanic Garden Press, St. Louis, Missouri. 1181 pp.

Appendix 1. RFSS Plant Descriptions Key to Global and State Ranks o G1/S1 - Critically imperiled – because of extreme rarity or because of some factor(s) making it especially vulnerable to extirpation from the state. Typically 5 or fewer occurrences or very few remaining individuals (<1000). o G2/S2 - Imperiled – because of rarity or because of some factor(s) making it very vulnerable to extirpation from the nation, state. Typically 6 to 20 occurrences or few remaining individuals (1000 to 3000) o G3/S3 - Vulnerable – either because rare and uncommon, or found only in a restricted range (even if abundant in some locations), or because of other factors making it vulnerable to extirpation. Typically 21 to 100 occurrences or between 3000 and 10,000 individuals. o G4/S4 - Apparently secure – uncommon but not rare and usually widespread. Possible cause of long-term concern. Usually more than 100 occurrences and more than 10,000 individuals. o G5/S5 - Secure – common, widespread, and abundant. Essentially ineradicable under present conditions. Typically with considerably more than 100 occurrences and more than 10,000 individuals.

RFSS Species

1. Appalachian Bugbane (Actaea rubifolia) Appalachian bugbane is a tall, slender perennial herb that occurs in portions of Virginia, Tennessee, Kentucky, Indiana, and Illinois. It flowers from July through October. This species is limited in range and there are approximately up to 80 occurrences known, approximately 50 of which, are extant.

Appalachian bugbane has been given a Global Heritage Status Rank of G3 by The Nature Conservancy in 2001 because of its rarity range-wide (NatureServe 2017) (http://www.natureserve.org/). Threats range- wide include logging, land-use change and unregulated recreational use. It is possibly extirpated in Alabama (1 county), critically imperiled in Indiana (2 counties), imperiled in Illinois (7 counties), Kentucky (4 counties), and Virginia (3 counties), and vulnerable in Tennessee (18 counties). Sightings in Pennsylvania are presumed to be exotic or introduced to the state. Many of the counties above list this species as extirpated or possibly extirpated. This species was considered “C2” by the US Fish and Wildlife Service and has been under review for federal endangered species status listing (NatureServe 2017).

Appalachian bugbane is found within Pope, Gallatin, Jackson, Johnson, Saline, and Hardin Counties. A report exists for Massac County on private property, but the population may be extirpated because of cattle grazing; the threat is not so much of this species being eaten as it is in the trampling associated with grazing. At least 26 populations are located in southern Illinois and include Ferne Clyffe State Park (Miller 1999). In these areas it is found in rich woods on talus slopes and is considered rare. It grows on sandstone and limestone.

The primary threat to this species in southern Illinois has been unregulated equestrian use, and more recently, illegal equestrian use in closed natural areas. In at least two cases, the threat is illegal all- terrain-vehicle use in closed natural areas. Another threat is the aggressive multiflora rose, autumn olive and amur honeysuckle that are quickly invading the Forest and threaten to take over the habitat required for this species.

At least 18 of approximately 24 populations in southern Illinois are currently unprotected on Forest managed lands, 6 being protected within natural areas. These populations will continue to be adversely impacted by equestrian use and ATV use unless trails continue to be designated and horses are restricted to these trails. There are at least 6 populations on private land, one is protected at Ferne Clyffe State Park, 3 appear to have no immediate threats, 1 has an unauthorized user-developed equestrian/ATV trail through the population at the railroad right-of-way, and the last population lost portions of its population from a private logging event in 1994. This species is globally rare but found locally abundant in a few of its populations on the Forest.

2. Shining False Indigo (Amorpha nitens) Shining false indigo is a branching, leguminous shrub. It is a very rare species that has been documented from approximately 80 occurrences in Oklahoma, Arkansas, Louisiana, Alabama, Tennessee, Georgia, Kentucky, South Carolina, and Illinois. This species reaches its northern range limit in the thickets and streambanks of southern Illinois. It occurs in a variety of habitats within its range including dry rocky upland barrens-like habitat and prairies (Taft 2004a). In southern Illinois it generally blooms from May to June.

According to NatureServe (2018) primary threats to shining false indigo include the destruction of habitat through agricultural conversion, grazing, and hydrological perturbations, such as dams. Other threats are exotic species such as Japanese honeysuckle (Lonicera japonica) and buckthorn (Rhamnus cathartica). The Nature Conservancy assigned Amorpha nitens the Global Ranking of G3? in 1995 and has been determined it to be critically imperiled in Illinois, Alabama, Georgia, and Oklahoma, and vulnerable in Kentucky. It is possibly extirpated from Louisiana. It is currently not ranked or is under review in Tennessee, and Arkansas. NatureServe (2018) does not have it occurring in South Carolina but PLANTS database (USDA, NRCS 2018) does as well as some other literature.

In Illinois, shining false indigo is historically known from Alexander, Pope, Pulaski, and Saline Counties. The Pulaski location has not been relocated since 1968. The Pope and Saline locations occur on Forest- managed lands. One is along the Grand Pierre Creek discovered by John Taft (#504, June 22, 1988) (2 metapopulations on private land and a metapopulation on National Forest managed land) and the other within Cave Hill Research Natural Area, in the Saline River floodplain, found in the mid-1990s by Dan Spivey. However, during a recent visit by Beth Shimp late May 2012 and fall of 2017, no plants were visible in the Saline River floodplain. County removal of hazard trees and recent floods may be contributing to the lack of plants and further searches will need to be made in 2019. Historic populations were documented by E.J. Palmer in 1919 as occurring along the Ohio River banks but these have not been relocated. The Alexander County population was discovered by Steve Hill (collections #31788 and #31819) June 23, 1999 and reported to originally consist of four colonies totaling about 22 plants. Since this discovery, highway construction appears to have destroyed about half of the population (Taft 2004a).

3. Black Chokeberry (Aronia melanocarpa) Black chokeberry is a perennial shrub from the Rosaceae family. Nation-wide it’s habitat includes swamps, bogs, wet thickets, margins of ponds and lakes, beaver ponds, woods, moist high-elevation

ii forests, and rock outcrops. It occurs sparingly in northeastern Illinois. In southern Illinois, it was first found by R.A. Evers in 1953, then again by D. Kurz in 1977 at Stoneface Research Natural Area in Saline County. It is also known from Johnson County at Ferne Clyffe State Park. Both locations are on sandstone bedrock above the cliffs or on the bluffs, quite different than other known habitats. Both locations have experienced a dramatic decrease in stem numbers and reduction in the size of the shrubs. The location in Saline County is currently not threatened by invasive species but is threatened by overshading from nearby trees. This species flowers between May and June.

The Nature Conservancy assigned black chokeberry the Global Ranking of G5 in 1984 (NatureServe 2017) but it is possibly extirpated in Delaware; critically imperiled in Iowa, Missouri, and Arkansas; vulnerable in North Carolina and Georgia; apparently secure in Kentucky and West Virginia; and secure in Virginia, New Jersey, New York, and New Brunswick, Nova Scotia, Quebec and Ontario, Canada. It is unranked or under review in 19 states including Illinois.

4. Bradley’s Spleenwort (Asplenium bradleyi) Bradley’s spleenwort is an evergreen, perennial fern found within the eastern and midwestern United States excluding New England and the states north of Illinois. It was historically documented from 19 states. It reaches its northern range limit in southern Illinois where it is very rare and occurs primarily on sandstone cliffs and chert outcrops.

Primary threats to Bradley’s spleenwort in southern Illinois include drought conditions and over collecting. Drought conditions are associated by the destruction of habitat throughout much of the species’ range. Examples of activities leading to drought conditions range-wide include strip mining activities, logging, rock climbing, and adjacent road and trail use. Japanese honeysuckle also poses a threat to this species and Nepalese browntop appears to be spreading down the cliff faces, which could also threaten this small fern by taking over its habitat. The Global Ranking by The Nature Conservancy was determined to be a G4 in 1993 (NatureServe 2019). This species is possibly extirpated in New York and West Virginia; vulnerable in Kentucky; imperiled in North Carolina, Virginia, Tennessee, Alabama, and Georgia; and critically imperiled in Illinois, Indiana, Ohio, Pennsylvania, New Jersey, Maryland, Oklahoma, and South Carolina. It is not ranked or is under review by Missouri, Arkansas, and Louisiana. Through the risk analysis, this species was retained on the RFSS list by the Forest to aid in its protection.

Bradley’s spleenwort has been found within Saline, Jackson, and Union Counties on the Forest. It may occur at the Crab Orchard Wildlife Refuge in Williamson County. It was first discovered in Illinois in Randolph County at Piney Creek, west of West Point by Robert H. Mohlenbrock in 1954. On March 6, 1955 he discovered another population (collection #4988) along the Jackson County extension of the creek (Mohlenbrock 1955). It is known to occur on the Forest within the LaRue-Pine Hills/Otter Pond (shaded, cherty slope, 15 to 20 individuals) and Cave Hill Research Natural Areas (bluff face, 1 to 3 individuals; discovered by Steve Olson on June 1, 1986), Panther Den Wilderness Area (bluff face, 9 individuals; first discovered by R.A. Evers September 15, 1964, then re-documented by Mark Basinger on October 29, 1993, collection #7852), and Garden of the Gods Ecological Area (R.A. Evers, June 29, 1966). Each of these sites has only a few plants per population. The Garden of the Gods population was last documented in 1980 as being scattered on the eastern cliff faces and overhangs. A recent discovery of one plant was found at Sand Ecological area during 2019 by Christopher Benda. A single plant was seen by Elizabeth Longo on September 12, 2019 at Sand Ecological Area (Pope Co.) and may have been the same one.

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5. Blackstem Spleenwort (Asplenium resiliens) Blackstem spleenwort is a wiry evergreen fern (spleenwort) that occurs in south-central and eastern United States. It reaches its northwestern margin of its range in southern Illinois where it is now only known to still be extant at one location on a limestone ledge.

According Herkert and Ebinger (2002), the primary threat to blackstem spleenwort in Illinois is over- collection. Japanese honeysuckle also poses a threat to this species and Nepalese browntop appears to be spreading down the cliff faces, which could also threaten this small fern by taking over its habitat. The Nature Conservancy assigned this species the Global Ranking of G5 in 1984 but it is unranked or under review in 11 southern states; presumed extirpated in Louisiana; possibly extirpated in Ohio; critically imperiled in Nevada, Utah, Colorado, Illinois, Indiana, Mississippi, South Carolina, Pennsylvania, and Maryland; imperiled in Kansas and North Carolina; vulnerable in West Virginia; and apparently secure in Kentucky, Georgia, and Virginia (NatureServe 2019).

In Illinois, blackstem spleenwort is historically known from Alexander, Jackson, and Union Counties. Records for these locations are scanty but information leads one to believe that the two Alexander locations have not been relocated for over 30 years, the Jackson County location at Devil’s Bake Oven (another collection is noted as Grand Tower, however, the location is described for Devil’s Bake Oven as being an exposure of Grand Tower Limestone and Lingle Formation), on thin soils of the limestone cliff, may still be present but has not been observed for over 10 years (private property), and the Union County locations at LaRue-Pine Hills/Otter Pond Research Natural Area (2 possible stations, shaded limestone cliff) have not been seen since 1985 and 1987, respectively (one population with 8 to 10 plants and another with only 1 individual near Otter Pond). One of the populations was first discovered by R.A. Evers on June 14, 1950; however, John Schwegman located a population across from Winter’s Pond in March 31, 2005. This original population was not found but a single plant was seen in May 2010 on the limestone bluff face near this location. This is believed to be the only extant population (with only one individual) at LaRue-pine Hills/Otter Pond RNA pending further searches. This plant was seen again by Elizabeth Shimp. A collection by Robert H. Mohlenbrock was documented as being discovered December 26, 1954 (collection #4948) at Grassy Knob (Mohlenbrock 1956). If these populations are still present, they are, in fact, susceptible to over-collecting. It is also possible that these populations may already have been collected to extirpation except for the newest population found. Further searches for these populations are needed and collections should be prohibited where restrictions are not yet enforced.

6. Twining Screwstem (Bartonia paniculata) Twining screwstem is an annual or perennial herb of wet peat bogs and sands and occurs in the southeastern United States and north along the Atlantic Coast. Its northern interior range limit is in the acid seep springs of extreme southern Illinois (Herkert & Ebinger 2002). This species generally flowers between August and September (Mohlenbrock 2014).

The Nature Conservancy assigned this species the Global Ranking of G5 in 1984, but it is critically imperiled in Wisconsin, Illinois, Oklahoma, Ohio, New York, Maine, and District of Columbia; imperiled in Michigan, North Carolina, Delaware, and New Brunswick and Ontario, Canada; vulnerable in Indiana, Pennsylvania, Maryland, Virginia, Georgia, and Newfoundland, Canada, and apparently secure in Kentucky and Nova Scotia. It is unranked or under review in 14 states (NatureServe 2018). It was presumed extirpated in Illinois until it was identified in five Forest natural areas in Pope County during

the early 1990’s (see below). Primary threats to Bartonia paniculata in Illinois are habitat loss (woody and shade-tolerant species encroachment, and Japanese honeysuckle and Nepalese browntop invasion), and hydrological changes (Basinger 2009).

This species occurs exclusively in and adjacent to acid gravel seeps and springs within Pope County in Illinois. These populations are known from Massac Tower Springs, Poco Cemetery North, Cretaceous Hills (mesic upland forest), Kickasola Cemetery, and Snow Springs Ecological Areas. The Snow Springs population (seep springs) was first documented in 1967 (Schwegman 1969) and the now-dehydrated area is dominated by shading red maple and river birch. This species was seen during 2007 by Elizabeth Shimp while the natural boundaries were being posted at Snow Springs; a few hundred plants were noted scattered in the area. Shannan Sharp observed 17 plants there September 17, 2019. The Cretaceous Hills population at Sphagnum Springs was discovered in 1967 (Schwegman 1969) and relocated on November 2, 1995, with at least 3 plants were noted (E. Ulaszek and D. Spivey collection #3060). Shannan Sharp observed 2 plants at this site on August 30, 2019, and subsequently discovered 2 other sites on September 4, 2019 in this natural area—61 plants near Azotus Spring and a single plant at North Long Springs. The Poco Cemetery North population (dry-mesic barren) was discovered October 21, 1994; 20 plants were seen (J. Shimp collection #5376). The Kickasola Barrens “New Spring” location (acid gravel seep) was collected on September 27, 1994 (E. Ulaszek collection #2289). This location was first documented by Lawrence Stritch on October 14, 1992 following a prescribed burn, which was conducted on March 5, 1992; he had found 20 plants at that time. Shannan Sharp relocated this population on September 17, 2019; she found about 60 plants that were in the middle of a heavy infestation of Nepalese browntop. John and Martha Schwegman discovered a population of about 25 plants at Massac Tower Springs on October 3, 2005. Shannan Sharp found about 25 plants there on August 8, 2017. After treating herbicide treating Nepalese browntop for 3 years and a prescribed burn at this site, Shannan Sharp counted about 300 plants on September 17, 2019.

7. Supplejack (Berchemia scandens) Supplejack is a perennial, high-climbing woody vine that occurs in the southeastern United States. It reaches its northern range limit in the Shawnee Hills Natural Division of Illinois (Herkert & Ebinger, 2002). It generally blooms from April to June (Mohlenbrock 2014). The single known population in Illinois is protected in a Forest natural area in an upland forest adjacent to pine plantation along a fire line. This population was discovered by John Schwegman in 1977. Elizabeth Shimp and Jason Rose last monitored it during July of 2019. The population appeared healthy, although several non-native species (multiflora rose, amur honeysuckle, autumn olive, Japanese honeysuckle, and Nepalese browntop) surrounded it in all directions.

It is critically imperiled in Illinois and Kentucky, and secure in Virginia and North Carolina. It is not ranked or under review in the 11 lower states. It was listed as a G5 in 1985. In Illinois the State lists it as endangered and in Kentucky it is listed as state threatened. It is known from 3 counties in Kentucky; however, it is possibly extirpated in Hickman County (NatureServe 2018).

8. Sparselobe Grapefern (Botrychium biternatum) Sparselobe grapefern is a perennial, evergreen fern with fleshy to nearly fibrous roots that grows up to 35 cm tall. Its range is the southeastern United States. It reaches its northern range limit in southern Illinois, where it has been found at open hillsides, edges of old fields, and within the woodlands, especially within mixed hardwood and pine. It is known from Alexander, Jackson, Johnson, Pope, Saline,

v and Union counties. In southern Illinois it is found primarily in pine stands but will appear in hardwood stands, as well. Japanese honeysuckle and Nepalese browntop are the two aggressive non-native species that are often present in its habitat and can pose a threat to it. In pine plantations, there are additional non-native species that could compete with this fern.

The Nature Conservancy assigned Botrychium biternatum the Global Ranking of G5 in 1985. It is listed as critically imperiled in Illinois and Missouri; imperiled in Ohio; vulnerable in Indiana, apparently secure in North Carolina and Kentucky; and secure in Virginia, Georgia, and Delaware. It is not ranked or under review in 13 southeastern states (NatureServe 2017).

9. Nottoway Valley Brome (Bromus nottowayanus) Nottoway Valley brome is a perennial grass that occurs in colonies. It is found in deep or partial shade of mature hardwood forests on rich bottomland terraces and floodplains or the rich adjoining slopes of streams. It is also found in moist, wooded ravines. In Illinois, this species flowers between June and August (Mohlenbrock 202).

The Nature Conservancy assigned this species the Global Ranking of G3G5 in 2003. It has been determined to be critically imperiled in Illinois, Kansas, North Carolina, New York, and Maryland; imperiled in Arkansas and Tennessee; vulnerable in Missouri and Virginia, and apparently secure in Ohio and Ontario, Canada. This species is not ranked or is under review by Texas, Oklahoma, Alabama, Georgia, Iowa, Indiana, and New Jersey (NatureServe 2018). It is also known from two counties in Michigan at one location in each county and is also not ranked there (USDA, NRCS 2018).

The primary threat to Nottoway Valley brome is habitat loss through logging. Other threats include equestrian use, other human use, and habitat encroachment by invasive species, both non-native and native, such as coralberry (Symphoricarpos orbiculatus) (NatureServe 2018).

In Illinois, Nottoway Valley brome is rare, having been found in only a few, scattered counties. It is known from Cook, Stark, Woodford, and Peoria Counties in northern Illinois, but specimens are reported to have been collected in Adams and Brown counties. In southern Illinois it is known from three collection sites near Cedar Lake in Jackson County and one in Pope County; Tom Heineke reported finding this species on May 10, 1976 (collection #1488) in mesic to dry woods in Jackson County. John Schwegman found a few plants on a north-facing limestone slope in the woods at Copperous Branch Ecological Area in Pope County on July 19, 2002. That site is currently being over shaded and invaded by Nepalese browntop.

10. American Bluehearts (Buchnera americana) American bluehearts is a hemiparasitic plant, living off the roots of several other plant species. It occupies sandy or gravelly soils of upland woods or prairies. In Illinois, it is known from prairies and fields. It occurs primarily in west central Illinois, with additional occurrences found in one extreme northern county and one in a southern county (Pope). It is historically known from 13 Illinois counties, although most collections were made during the 1970’s or earlier (Danderson 2004). In Illinois, this species has been seen in flower from mid-June through September (Mohlenbrock 2014).

The Nature Conservancy assigned this species the Global Ranking of G5? in 1994 and has historical occurrences listed for 25 states and Ontario but it is presumed extirpated from Michigan, Pennsylvania, New Jersey, and the District of Columbia; and possibly extirpated from New York, Delaware, and

Maryland. It has been determined to be critically imperiled in Indiana, Virginia, Georgia, North Carolina, and Ontario, Canada; imperiled in Ohio and Texas; and vulnerable in Illinois, Kentucky, and Tennessee. This species has been extirpated from the periphery of its range but is apparently secure in Missouri, Arkansas, and Alabama. It is not ranked or is under review in Kansas, Oklahoma, Louisiana, Mississippi, Florida, and South Carolina. The primary threat to American bluehearts is habitat loss. Fire suppression in prairies has led to forest succession where the sites convert to woodlands and become shaded. Without the natural regime of fires, open prairie areas will continue to close in and may lead to the demise of this species (NatureServe).

American bluehearts is very rare in southern Illinois (e-mail communication from John Schwegman to Elizabeth Shimp April 5, 2001). It grows as an annual or perennial and is restricted to the barrens communities of southern Pope County. John Schwegman monitored this species for several years and has determined that while it grows primarily as an annual, it can a parasitize composite species and grow as a biennial or perennial (Danderson 2004). It is known from Cretaceous Hills Ecological Area on Forest-managed lands (Azotus Field) and from the adjacent Cretaceous Hills Nature Preserve managed by the State of Illinois. According to Mr. Schwegman, like so many annuals of the prairie, this species disappears without fire. Although American bluehearts has not been seen in Azotus Field for over 20 years, it may still be present in the seed bank. During a recent visit in July 2019, Elizabeth Longo and Jason Rose observed a great influx of Nepalese browntop and intense shading of young trees in the Azotus field. No American bluehearts were found.

11. Porter’s Reedgrass (Calamagrostis porteri var. insperata) Porter’s reedgrass is a perennial grass that has a very limited distribution in the central United States. Its range extends from southern Ohio, southwest to Kentucky, Illinois, Missouri and Arkansas. Its habitat includes dry rocky woods usually with a northern slope, on dry limestone cliffs and sandstone outcrops. This species rarely flowers in Illinois. Flowering time is from June through September (Hill 2003b).

Porter’s reed grass was assigned a G4T3 Global Ranking by The Nature Conservancy in 1996 (last reviewed in 2010). It is only known from 6 states and is presumed extirpated from Arkansas, critically imperiled in Illinois, Indiana, and Kentucky, imperiled in Ohio, and vulnerable in Missouri. Approximately 80 occurrences are known throughout this species’ range (NatureServe). Threats to this grass include canopy closure as a result of natural forest succession or succession due to fire suppression, clear- cutting, grazing, soil compaction, recreational use of its habitat, and loss of habitat, primarily form agriculture (Hill 2003b, and NatureServe).

In Illinois, Porter’s reedgrass has only been found in Pope County. One site is on state land at a state nature preserve. The other sites are located on the Shawnee National Forest in three natural areas: Bell Smith Springs Ecological Area, Hayes Creek/Fox Den Ecological Area, and Lusk Creek Canyon Ecological Area. Some populations on the Forest are threatened by Nepalese browntop infestations and increasing woody encroachment. At Bell Smith Springs, lack of sunlight has reduced the vigor of Porter’s reedgrass and severely reduced flowering and fertility.

12. Broadwing Sedge (Carex alata) Broadwing sedge is a perennial tufted sedge with culms reaching up to 1.4 m high. It is a species of wet ground (Mohlenbrock 2014) and is found in the eastern United States and Midwest, including Ontario, Canada (NatureServe). This species flowers during May in southern Illinois (Mohlenbrock 2014).

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The Nature Conservancy assigned broadwing sedge the Global Ranking of G5 in 1984 and has determined it to be vulnerable in Indiana, Ohio and North Carolina; imperiled in Pennsylvania and Missouri; critically imperiled in Texas, Arkansas, Kentucky, Illinois, Connecticut, and Ontario, Canada; apparently secure in New York and New Jersey; and secure in Virginia, and Delaware. It is possibly extirpated in New Hampshire. It is not ranked or is under review in 11 eastern states (NatureServe).

In southeastern Illinois, this sedge is rare and local, and found in swamps and floodplain forests and wet ground. It is presently known from the following localities in the state; a private swamp border in Pope County (3 colonies first observed by John Schwegman on March 15, 1977 and last observed June 13, 2001), a flatwoods in a state fish and wildlife area (Massac County, 1987), Oakwood Bottoms in Jackson County (Rick Phillippe, June 24, 1993), and near Lake Glendale next to a dam (2 clumps found by John Schwegman June 7, 2010, Pope County). Separate searches by John Schwegman and Beth Shimp at Lake Glendale did not detect this species during 2017. There is a report of this species possibly being at another Pope County location (2001) but the details were unavailable at the time of this writing. There are also reports that this species once occurred in Cook and Wabash counties, but it is no longer extant at either site.

13. Prickly Bog Sedge (Carex atlantica) Prickly bog sedge is a very rare species that grows in swampy woods in Illinois. This species flowers from April to May (Mohlenbrock 2014).

The Nature Conservancy assigned this sedge the Global Ranking of G5 in 1984 (NatureServe 2018). It is ranked as critically imperiled in Illinois, Vermont, and New Brunswick, Ontario, and Quebec, Canada; vulnerable in North Carolina; apparently secure in Nova Scotia, Canada, West Virginia, Delaware, and Kentucky, and secure in New York, Virginia, Maryland, Mississippi, and Louisiana. It is unranked or under review in 20 states. (NatureServe)

On the Shawnee National Forest, it is known from the wooded seep springs in Pope County. It was found at 4 seep springs at Cretaceous Hills Ecological Area (Elizabeth Shimp, John Schwegman, and Martha Schwegman on May 30, 2007), 1 at Dean Cemetery West EA, 1 at Massac Tower EA, 1 at Kickasola Cemetery Barrens EA, and 1 at Snow Springs EA (collected by John Schwegman during 1967 and recently verified 2005 and 2009 at most sites). Two nearby locations occur on private property south of Kickasola Ecological Area. An unverified report states that this species is also known from private property in Pulaski County.

These populations are threatened by non-native invasive plants, with Nepalese browntop as the main threat and with Japanese honeysuckle running second (Basinger 2009). These two aggressive species are taking over the seep springs that are not covered by the Invasive Species Management EA (2014). The seep springs that were included in the EA are benefitting from the use of selective herbicides to control non-native invasive infestations, thereby protecting rare species such as prickly bog sedge.

14. Brome-like Sedge (Carex bromoides) Brome-like sedge grows in low woods, seep springs, swamps, and prairie bogs in Illinois, becoming very rare in southern Illinois. This species flowers from April to May (Mohlenbrock 2014).

The Nature Conservancy assigned brome-like sedge the Global Ranking of G5 in 1984. It is ranked as critically imperiled in Delaware; imperiled in North Carolina, Illinois, and Arkansas; vulnerable in West

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Virginia and Quebec, Canada; apparently secure in Kentucky, Mississippi, Maryland, and New Brunswick and Nova Scotia, Canada; and secure in Virginia, New York, and Ontario, Canada. It is unranked or under review in 21 states (NatureServe 2017).

Brome-like sedge is known from eight northern Illinois counties, and from Jackson, Johnson, and Pope Counties in the southern part of the state. In Johnson County, one location on private property and the other is at Grantsburg Swamp (Mark Basinger and Elizabeth Shimp on May 2, 1994; Shannan Sharp photographed this species at Grantsburg Swamp on April 12, 2018). There are four known locations in Pope County, all at seep springs. It was first collected at Cretaceous Hills by John Schwegman (1969), then re-collected by John Schwegman on May 10, 2005; Elizabeth Shimp, John Schwegman, and Martha Schwegman re-located it on May 30, 2007. John Schwegman found this sedge at Snow Springs prior to 2006. He collected this species at Reddick Hollow on May 17, 2005. John White and Elizabeth Shimp found it at Kickasola Cemetery Barrens EA on August 9, 2013. Information on the Jackson County population was not available at the time of this writing.

15. Cherokee Sedge (Carex cherokeensis) Cherokee sedge is a perennial with short-to long-creeping, stout rhizomes that form dense colonies; previous season’s sheaths persist and are noticeable beneath the basal leaves. Flowering stems are 30- 60 cm tall and blooms from April through June. Its range is from Georgia to Texas, north to North Carolina, Missouri, Illinois; it is uncommon in southern Missouri and Illinois. It is found in bottomland forests, acid seeps, margins of sinkhole ponds, openings of dry upland forests, dolomite glades, and roadsides (Yatskievych 1999) and within wet depressions of rarely used roads (personal observations).

Cherokee sedge was given the Global Heritage Status Rank of G4G5 by The Nature Conservancy in 1988. It is listed as critically imperiled in Kentucky and North Carolina, imperiled in South Carolina, apparently secure in Missouri, and secure in Arkansas and Mississippi. It is considered an exotic in Virginia. It is not ranked or under review in Oklahoma, Texas, Louisiana, Alabama, Florida, Georgia, and Tennessee (NatureServe 2017).

According to Mohlenbrock (2014), Cherokee sedge is only known from Alexander, Jackson, and Union, in Illinois. No information was found for Jackson and Williamson Counties at the time of this writing. Steven Hill found a population in Alexander County on May 3, 2000 on the east side of IL Route 127, south end of Tamms, on the west side of the original Cache River (#32294). Hill re-confirmed this population on June 6, 2002. David Ketzner and Dennis Keene found a population in Union County at the Union County State Conservation Area in a wet-mesic floodplain forest on July 23, 2003 (#3301).

Mark Basinger identified this plant in Hardin County in 2009 at the Lee Mine area (Jody Shimp, personal communication with Shannan Sharp). Elizabeth Shimp and Shannan Sharp found other locations of Carex cherokeensis in the Lee Mine area on August 4 and 7, 2015. In 2015, Shimp continued to find more locations along wet depressions in the Lee Mine area predominantly along and on infrequently used grassy roads. A few populations were within pine stands. Nepalese browntop (Microstegium

vimineum) is the main threat to this species at Lee Mine. On October 18, 2017, Elizabeth Shimp and Johnny Walker found a few clumps of this species in wet depressions along an infrequently used grassy road in Pope County just south of the Pleasant Valley Barrens Ecological Area. 16. Cypress-knee Sedge (Carex decomposita) Cypress-knee sedge is a perennial tufted sedge with thick, woody rhizomes. It is a species of swamps, often on floating logs or buttressed tree bases (Mohlenbrock 2011), ranging from New York to Michigan and south to Florida and Texas (USDA, NRCS Plants Database). This species reaches its northwestern range limit in the cypress swamps of southern Illinois (Herkert & Ebinger 2002). In southern Illinois, this species flowers June through August (Mohlenbrock 2011).

The Nature Conservancy assigned cypress-knee sedge the Global Ranking of G3G4 in 2010. The primary threat to it is loss of its native habitat through land conversion and drainage. Its spotty distribution, specific habitat requirements, and habitat destruction are accelerating the decline of this species. It is known from 22 states but is listed as presumed extirpated in Michigan and possibly extirpated in New York and the District of Columbia. It is ranked critically imperiled in Illinois, Ohio, Delaware, Maryland, Alabama, Oklahoma, and Texas; imperiled in Indiana, Kentucky, Tennessee, Virginia, North Carolina, South Carolina, Georgia, and Arkansas; and vulnerable in Missouri, Louisiana, and Mississippi. It is not ranked or is currently under review in Florida. The primary threat to this species is loss of native habitat (habitat conversion and drainage). The spotty distribution, specific habitat requirements, and continued habitat destruction are leading to an accelerated decline of this species (NatureServe).

The distribution of cypress-knee sedge is also spotty in southern Illinois, occurring in isolated patches within swamps. Opportunities for seed dispersal are limited, with shrinking numbers of protected swamps and permanent wetlands. This species requires high-quality water conditions without chemical pollutants or pesticide runoff. Hydrologic alterations, such as water drainage, also threaten its habitat, as well as woody encroachment of swamps from the absence of fire (NatureServe).

Presently, cypress-knee sedge occurs in Alexander, Johnson, Pope, Pulaski, and Union Counties. A Gallatin County population on private property was destroyed several years ago by logging activities (Herkert 1991, Herkert & Ebinger 2002). On the Forest, this species is known from Grantsburg Swamp Ecological Area in Johnson County, and from LaRue-Pine Hills/Otter Pond Research Natural Area (first documented by W. Bailey and J. Swayne on May 19, 1952) in Union County. Cypress-knee sedge has also been documented at Cypress Creek National Wildlife Refuge in Alexander County, at the Cache River Land and Water Reserve in Johnson County, at Round Pond Nature Preserve in Pope County, and a Cypress Slough in Pulaski County.

17. Giant Sedge (Carex gigantea) Giant sedge is a perennial cespitose sedge that can also be found growing singly, from fibrous roots with long connected rhizomes. It is a species of swamps and wet woods primarily on the coastal plain from Delaware south to Florida, east to Texas and north in the Mississippi Embayment to southern Illinois and Indiana. Its northern range limit is southern Illinois, where it is known from wet woods and swamps. In southern Illinois, this species flowers from May through September.

The Nature Conservancy assigned giant sedge the Global Ranking of G4 in 1984. It is historically known from 18 states and but is listed as critically imperiled in Illinois, Indiana, Arkansas, Kentucky, and Missouri, and vulnerable in Maryland and Delaware. It is apparently secure in Virginia and North

Carolina, and secure in Mississippi. In the states of Oklahoma, Texas, Louisiana, Tennessee, Alabama, South Carolina, Georgia, and Florida it is currently not ranked or is under review. The primary threat to this species is loss of native habitat (habitat conversion and drainage). The spotty distribution, specific habitat requirements, and continued habitat destruction are leading to an accelerated decline of this species. (NatureServe 2017).

In southern Illinois giant sedge is historically known from Jackson, Johnson, Massac, Pulaski, and Union counties. On the Forest, this species is known from Grantsburg Swamp Ecological Area in a bottomland hardwood forest (Mark Basinger and John Rundle July 5, 1994; collection #8709 and #8725) in Johnson County and at LaRue-Pine Hills/Otter Pond Research Natural Area north of Otter Pond (Union County) in a wet woods near the swamp (last observed November 28, 1967). A population discovered at Sielbeck Woods (private) in Massac County by Mike Homoya in 1976 was relocated and vouchered by John Schwegman August 1, 1997 and again observed September 6, 2001 by Mark Guetersloh. The Pulaski County site at Post Creek Cutoff (private) was discovered on June 23, 1992 by John Taft. Documentation for the Jackson County occurrence was lacking at the time of this writing. Opportunities for seed dispersal are limited with reduced numbers of protected bottomland hardwoods, swamps and permanent wetlands. Like cypress-knee sedge, this species requires high-quality conditions without hydrologic alterations, such as water drainage, or chemical pollutants.

18. Greater Bladder Sedge (Carex intumescens) Greater bladder sedge is a perennial cespitose sedge with culms reaching 80 cm tall. Its range is the eastern United State and adjacent Canada. In Illinois it occurs in forested wetlands and swamps. This species flowers between May and September in southern Illinois.

The G5 Global Ranking for this species was assigned by The Nature Conservancy in 1984. It is critically imperiled in Labrador, Canada, Illinois, and Wyoming. It is also listed as vulnerable in South Dakota and Manitoba, Canada. It is apparently secure in Newfoundland, Canada and West Virginia and secure in Arkansas, Mississippi, North Carolina, Virginia, Kentucky, Delaware, New Jersey, New York, Ontario, Quebec, New Brunswick, Nova Scotia, and Prince Edwards Island, Canada. It is not ranked or is under review in 23 of the United States (NatureServe 2017).

In Illinois, greater bladder sedge has been found in Alexander, Johnson, Pope, and Saline Counties, with several on Forest Service lands. In Jackson County it was found in Oakwood Bottoms by Chris Benda 25 June 2018 (Biotics). In Johnson County it is known from the Grantsburg Swamp Ecological Area (LR Stritch #2223 10 June 1991; J.P. Shimp, RH Mohlenbrock and LR Stritch #970 28 May 1992); at Bay Creek (Chris Benda 9 September 2011 (Biotics)); and north of Reevesville (Chris Benda 9 September 2011 (Biotics)). In Pope County it has found at several areas on the Forest— EL Shimp and AS Biagi #4023 15 June 1992; MA Basinger and EL Shimp #5717, #5770, #5822 21 June 1993, Big Grand Pierre Creek; MA Basinger and J Rundle #8738 11 July 1994, #8763 12 July, 1994; JP Shimp and MA Basinger #5293 15 Aug 1994; EF Ulaszek and EL Shimp #2814 31 July 1995.

19. False Hop Sedge (Carex lupuliformis) False hop sedge is a perennial, tufted sedge. It is uncommon in eastern North America, west to southwestern Quebec, Wisconsin and Louisiana. It is found scattered throughout Illinois and occurs in wet woods, wooded swamps, marshes, meadows, and roadside ditches. In southern Illinois, this species flowers from June through October.

False hop sedge was assigned the G4 Global Ranking for this species by The Nature Conservancy in 2000. This species has had widespread declines throughout its range. It is possibly extirpated in Iowa; critically imperiled Pennsylvania, New Jersey, Massachusetts, North Carolina, Arkansas, Maryland, Texas, and in Quebec and Ontario, Canada; imperiled in Wisconsin, Michigan, Indiana, Ohio, New York, Vermont, West Virginia, Virginia, Delaware, and Tennessee; and vulnerable in Illinois. It is apparently secure in Connecticut, Kentucky and Mississippi. It is not ranked or is under review in Minnesota, Missouri, Oklahoma, Louisiana, Florida, South Carolina, Georgia, and Maine. False hop sedge is threatened by the destruction of its native habitat. Damming of rivers, ditching, channeling, floodplain cultivation, and spring flood cycle interruptions are major threats of this species throughout its range. Another documented threat is ATV use (NatureServe 2017).

False hop sedge is listed as historically occurring in Alexander, Pope, Johnson, Jackson, Massac, Pulaski, Saline, Hardin, and Union counties. This species is not as common as once thought to be in Illinois because original specimens have been previously misidentified and found to be Carex giant sedge or hop sedge (Carex lupulina). It is possible that some of the county records may be misidentifications. This species is not listed as threatened or endangered in the State of Illinois, which makes tracking collections and records more difficult.

Until recently, specimens of false hop sedge collected in southern Illinois were over 40 years old. However, Mark Basinger collected this species at Horseshoe Lake Conservation Area on May 30, 1996 in Alexander County. Shannan Sharp collected it at Oakwood Bottoms in Jackson County on September 15, 2014 (#20 & #21), in an open-canopy, seasonally flooded area that is periodically prescribed burned. Before then, records from the Illinois Natural History Survey collections (specimen list provided to Elizabeth Longo Shimp by e-mail on December 17, 2004 from Loy R. Phillippe) indicate the following specimens at the herbarium: Alexander (Evers #30438, 20 June 1951, east of Miller City, lake shore; Evers #32872, 19 September 1951, southeast of Olive Branch, bottomland ditch), Pope (Evers #23561, 10 June 1950, east of Dixon Springs, marsh), Pulaski (Evers #19997, 25 August 1949, south of Ullin, marsh land), and Union counties (Henry #2203, 22 July 1966, LaRue Swamp, wet ground).

20. Black-edge Sedge (Carex nigromarginata) Black-edge sedge is a densely tufted perennial sedge with culms growing to 2.5 cm high. It is known from the southeastern United States, extending north to southern Illinois. It occurs at its northern range limit in Illinois, where it prefers open, dry-mesic rocky woods, especially where light gaps are present. This species generally flowers during April and May.

Black-edge sedge was assigned a G5 Global Ranking by The Nature Conservancy in 1994 (last reviewed in 2016). It is ranked as critically imperiled in Illinois and Ontario, Canada (only a single population exists in Ontario); imperiled in New York; vulnerable in West Virginia and North Carolina; possibly extirpated in Connecticut; apparently secure in Missouri, Kentucky, and Pennsylvania; and secure in Virginia, New Jersey, Delaware, Arkansas, and Mississippi. It is not ranked or is under review in 11 states. Threats to this species include canopy closure as a result of natural forest succession and fire suppression, and loss of habitat from clear-cutting. Clear-cutting allows shrubs to invade its typical open habitat and will outcompete this species. Non-native shrubs such as multiflora rose, autumn olive and amur honeysuckle are most likely to invade its habitat (NatureServe 2019).

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In Illinois, black-edge sedge has been found Alexander, Gallatin, Hardin, Jackson, Monroe, Montgomery, Pope, Union, and Wabash Counties. On the Forest this sedge was found at the Bean Ridge Area in Alexander County (1994 by Rick Phillipe); at Thacker Hollow in Gallatin County (2009 by Mark Basinger and Elizabeth Shimp); at Panther Hollow Research Natural Area in Hardin County (last observed on May 20, 2011 by Jody Shimp, Chris Benda, John VanDyke, and Chris Evans); at a couple sites in the Water fall area in Jackson County (Chris Benda June 26, 2019); at two sites in Lusk Creek Wilderness in Pope County (Mark Basinger May 17, 2000, and Jody Shimp, Chris Benda, John VanDyke, and Chris Evans May 27, 2011); and a historic record (Robert Mohlenbrock April 16, 1957) at LaRue Pine Hills in Union County. It has also been found on private land near Ozark Hills Prairie Research Natural Area in Union County.

21. Sharpscale Sedge (Carex oxylepis var. pubescens) Sharpscale sedge is a rare perennial sedge that occurs in dry-mesic to mesic woods and is confined to four states. The northern range limit of this species is in southern Illinois where it is known from one county. It blooms from April to May in Illinois.

This variety of sharpscale sedge was assigned the Global Ranking of G5?T3 by the Nature Conservancy in 1999. Until recently, it had only been known from Arkansas and Tennessee, but was recently documented in Mississippi. It is listed as critically imperiled in Tennessee, imperiled in Mississippi, and vulnerable in Arkansas (NatureServe). The State of Illinois does not recognize this particular variety, but lists the species as a whole as threatened (Herkert & Ebinger 2002). Threats to this species include canopy closure as a result of natural forest succession and fire suppression, and loss of habitat from clear-cutting, grazing, soil compaction, and recreational use (NatureServe).

This variety of sharpscale sedge was first found in Illinois on May 29, 1954 by Robert H. Mohlenbrock (#8632) on a dry slope of woods above a sandstone fluff at Blind Hollow in Hardin County. It was then re-discovered on May 27, 1993 along a stream in dry-mesic woods within Panther Hollow Research Natural Area, Hardin County (Jody Shimp collection #4310). It was found again in Panther Hollow on July 1, 1994 within a disturbed, dry-mesic woods adjacent to a pine plantation (Jody Shimp collection #5271, 5272, and 5273). Shimp also found the species along user-developed ATV trails near Camp Cadiz on April 28 and May 10, 1995 (collections #5407 and #5996, respectively). These were found in second growth early successional forests. On June 12, 1995, Eric Ulaszek and Mark Basinger found this species in a dry-mesic upland forest above a sandstone cliff about a mile from Battery Rock (collection #2502) and again on June 13, 1995 (no collection made) in a dry-mesic forest along the River-to-River trail near Battery Rock. Mark Basinger made the latest collections on July 8, 1998 within a dry-mesic upland forest and a pine plantation on a ridge along the Ohio River south of Sturgeon Hill (collections #11371 and #11372, respectively).

22. Drooping Sedge (Carex prasina) Drooping sedge is a perennial sedge with culms reaching 25-80 cm in height. If is found in northeastern United States and adjacent Canada. It occupies rich lowland forests in most of its range and is restricted to forested seeps and sandstone undercuts in Illinois. It flowers from May to June.

The Nature Conservancy assigned drooping sedge the Global Ranking of G4 in 1990. It is ranked as possible extirpated in Arkansas; critically imperiled in Illinois, Missouri and Mississippi; imperiled in South Carolina; vulnerable in Georgia, North Carolina, Wisconsin, and Quebec, Canada; apparently secure in New Jersey, Delaware, West Virginia, Virginia, and Ontario, Canada; and secure in Kentucky

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and New York. It is unranked or under review in 15 states. The main threat to this species is habitat destruction (NatureServe 2017).

In Illinois, drooping sedge is historically known from Jo Daviess and LaSalle Counties in the northern part of the state; Adams, Brown, Lawrence and Vermilion Counties in the central part; and Johnson and Pope Counties in the southern part. The populations in Adams and Lawrence Counties are in state parks and the Brown County population is on private land. No information for the Johnson County report was located at the time of this writing and may have been a species misidentification.

Drooping sedge is known from a single site on the Shawnee National Forest. It occurs in a single protected site within a wooded seep spring area at Gyp Williams Hollow Ecological Area (Pope County, collected by Mark Basinger on May 14, 1997). It was viewed there in the spring of 2017 by Elizabeth Shimp; no non-native invasive species were present at the seep area at that time. 23. Sand Hickory (Carya pallida) Sand hickory is a small tree growing up to 15 meters tall. It reaches its northwestern range limit in extreme southern Illinois, where it grows on dry wooded slopes (Herkert & Ebinger 2002). It blooms from April to May in Illinois (Mohlenbrock 2014).

Sand hickory was given the Global Heritage Status Rank of G5 in 1984 (NatureServe). It is listed as endangered in the state of Illinois (Herkert & Ebinger). Elsewhere it is listed as critically imperiled in Arkansas; imperiled in Indiana and Louisiana; apparently secure in Delaware, Kentucky, New Jersey, North Carolina, and Virginia; and secure in Maryland. It is unranked or under review in Alabama, Florida, Georgia, Massachusetts, Mississippi, South Carolina, and Tennessee (NatureServe).

There are records of sand hickory from Alexander, Hardin, Johnson, and Union Counties. It has also been found in central Illinois, but those records are historical. Most known locations of this tree are on the Shawnee National Forest. In Alexander County it has been found on Forest Service land at Opossum Trot Trail Botanical Area (although this may have been a mis-identification) and at Ozark Hill Prairie Research Natural Area, as well as on private land. In Hardin County it was found on the Forest at Keeling Hill South Ecological Area and on private land near Shawneetown. It was found at two sites on private land in Johnson County. In Union County, this tree has been found at Trail of Tears State Forest and at LaRue Pine Hills Research Natural Area on the Forest. 24. Fairywand (Chamaelirium luteum) Fairywand is a dioecious, perennial lily with a basal rosette of spatulate leaves. It is found infrequently in meadows, thickets, rich woods, mesic forests and bogs from Massachusetts south to Florida, west to Ohio, southern Indiana and Illinois, Arkansas, and Louisiana. It is disjunct in southern Ontario, Canada. This species reaches its northwestern range limit in extreme southeastern Illinois.

Fairywand was assigned a G5 Global Ranking by The Nature Conservancy in 1986 and last reviewed in 2001. It has been found in 23 states, the District of Columbia and Ontario, Canada. It is presumed extirpated in Ontario; critically imperiled in Illinois (endangered, Nÿboer & Ebinger), Indiana, New York, Massachusetts, Connecticut, and Delaware; imperiled in Louisiana, and vulnerable in Arkansas, Maryland, and New Jersey. It is apparently secure in Kentucky and secure in West Virginia, Virginia, and North Carolina. It is also listed as an introduced (exotic) species in Michigan and not ranked or under review in 8 states and the District of Columbia. Threats to this species include root and seed collection

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for medicinal purposes, canopy closure as a result of natural forest succession and fire suppression, and loss of habitat from clear-cutting and shelterwood cutting (NatureServe).

In southern Illinois it is found in low wooded hillsides in Hardin, Massac, and Pope Counties. On the Forest it is found along Burke Branch in mesic floodplain forest at Burke Branch Research Natural Area, in the little seep springs in the Cretaceous Hills Ecological Area (also in mesic upland forest), along the sandy banks of a dried stream at Massac Tower Springs Ecological Area, just outside of the protected barrens areas in southern Pope County in a dry-mesic open woods on a south facing slope, near the Ohio River, and outside of the Kaskaskia Woods Ecological Area in a ravine. Non-native species that threaten this lily are Nepalese browntop, Japanese honeysuckle, Amur honeysuckle, autumn olive, and multiflora rose. 25. Red Turtlehead (Chelone obliqua var. speciosa) Red turtlehead is a branching perennial in the figwort (snapdragon) family. It is a rare species of alluvial woods, swamps, low woods, and wet meadows, and ranges from Minnesota and Michigan south to Arkansas and Kentucky. There are accounts of historical populations of this species scattered throughout 25 counties in Illinois but only 12 are considered to be extant (Phillippe 2004a). This species flowers from August through September and bears fruit September through October (Ambrose et al. 1994).

The Nature Conservancy assigned red turtlehead a Global Ranking of G4T3 in 1994 and has determined it to be vulnerable in Illinois, Indiana, and Kentucky, critically imperiled in Michigan, and possibly extirpated in Arkansas. It is not ranked or is under review in Iowa, Missouri and Minnesota (NatureServe 2017). Southern Illinois, southern Indiana and western Kentucky are considered to be strongholds for this species; however, trends are not well known, and populations are likely declining across its range due to loss of habitat (Ambrose et al. 1994). Primary threats include the physical destruction of habitat and artificial changes in hydrology. Succession may also threaten this species as it does not do well with competition from robust shrubs and vines under a closed canopy (NatureServe 2017). Management activities including selective thinning, maintenance of a dynamic hydrological cycle and periodic disturbances may be necessary to protect suitable its habitats (Ambrose et al. 1994).

Red turtlehead is found scattered throughout Illinois and has been reported from eight of the southernmost counties. Records from the Illinois Natural History Survey collections (specimen list provided to Elizabeth Longo Shimp from Loy R. Phillippe) and Iverson et al. (1999) indicate that the following specimens are available at the herbarium: Alexander (last seen 1931), Gallatin (last seen 1960), Hardin (last seen 1988), Jackson (last seen 1989), Johnson (separate locations 1931, 1931/1978, 1960, 1969, 1990/1992), Massac (1951), Pulaski (1931) and Union (1960) counties. The only extant population on the Shawnee National Forest may be the Johnson County collection of August 31, 1990 at Grantsburg Swamp Ecological Area by Rick Phillipe. It is unclear if the collection made in 1992 was actually on forest service managed land or on private property, nor is it clear if the section indicated on the record is accurate, however it was documented along the margin of a swamp. 26. Striped Prince’s Pine (Chimaphila maculata) Striped prince’s pine is a perennial herb with stems reaching 25 cm tall. It occurs in the Eastern United States and adjacent Canada. In Illinois, it generally occurs in dry-mesic upland forests, where it flowers from June to July.

The Nature Conservancy assigned this species the Global Ranking of G5 in 1984. Its Conservation Status is presumed extirpated in Quebec, Canada; critically imperiled in Illinois (endangered) and Ontario, Canada; imperiled in Maine, Mississippi, and Vermont; vulnerable in Arizona and Indiana; apparently secure in New York; and secure in Delaware, the District of Columbia, Kentucky, New Jersey, North Carolina, Virginia, and West Virginia. It is not ranked or is currently under review in Alabama, Connecticut, Florida, Georgia, Massachusetts, Michigan, New Hampshire, Ohio, Pennsylvania, Rhode Island, South Carolina, and Tennessee. This species is vulnerable to soil disturbance and compaction, as well as reduction in canopy cover. It is threatened by logging, moderate to high intensity fire, as well a mild disturbance such as walking (NatureServe).

Richard and Jean Graber collected this species on May 30, 1982 in a 40-year old loblolly pine plantation in Pope County. It is also known from the Lusk Creek Wilderness (Chimaphila Site, in upland woods by James Fralish in the 1980’s). In Hardin County, Alicia Biagi, Mark Basinger, and Amanda Poole collected it on July 28, 1993 in a white oak plantation at Camp Cadiz. Elizabeth Shimp found two plants at the Pine Ridge Campground at Pounds Hollow in the late 2000’s. She also found it in the mid 1990’s just outside of the Russell Cemetery Barrens Ecological Area in a pine plantation. Collections were not made at either site because of the small populations. Non-native species that threaten this lily are Nepalese browntop, Japanese honeysuckle, Amur honeysuckle, autumn olive, and multiflora rose. 27. Carolina Thistle (Cirsium carolinianum) Carolina thistle is a fibrous-rooted biennial, 0.5-1.5 m tall that occurs in the southeastern United States. It is a species of dry, acidic woodlands and reaches its northern range limit in extreme southern Illinois. It generally flowers from June through July in Illinois.

The Nature Conservancy assigned this species the Global Ranking of G5 in 2003. Its Conservation Status is critically imperiled in Virginia; imperiled in Ohio, Indiana, and North Carolina; and vulnerable in Kentucky and Georgia. It is not ranked or is currently under review in Arkansas, Alabama, Louisiana, Mississippi, Missouri, Oklahoma, South Carolina, Tennessee, and Texas (NatureServe). In Illinois, this species was listed as threatened until 1994, when it was determined to be more common than formerly thought (Mankowski).

Carolina thistle has been found in Hardin, Jackson, Johnson, Pope, and Saline Counties in Illinois. In Saline County, Elizabeth Shimp collected it at Dennison Hollow Research Natural Area (RNA) on 24 June 1992 in Saline County. Jody Shimp collected it at Simpson Barrens Ecological Area in Johnson County. This species is also known from a few plants at Cave Hill RNA in Saline County and Bell Smith Springs Ecological Area and at Gyp Williams Hollow Ecological Area in Pope County. Plants have been seen at the Williams Hill tower site; however, mowing has forced this species to virtually disappear here. This species was also found at Panther Hollow RNA in Hardin County by Jody Shimp in the 1990’s and by David Kurz in the 1980’s in the Buttermilk Hill area in Jackson County. For the most part, non-native species are not currently threatening this species at Cave Hill and Bell Smith Springs; however, it is inevitable that non-native species will gradually move into its habitat if not controlled or eradicated from adjacent areas. 28. Kentucky Yellowwood (Cladrastis kentukea) Kentucky yellowwood is leguminous tree that grows up to 15 meters tall. It occurs in the southeastern United States (native to 17 states) and the Ozarks. A plant of rich woods and calcareous bluffs, this

xvi species reaches its northern range limit in southern Illinois. Unlike other species in its subfamily, Kentucky yellowwood’s roots do not fix nitrogen.

The Nature Conservancy assigned this species the Global Ranking of G4 in 1984. Kentucky yellowwood is critically imperiled in Illinois, Louisiana, and South Carolina; imperiled in Indiana, Oklahoma, Mississippi, and North Carolina; and vulnerable in Missouri, Kentucky, Alabama, and Georgia. This species is considered introduced (exotic) in New York, Maine, Massachusetts, and Ontario, Canada. It has been determined to be secure in Tennessee and is not ranked or is under review in Ohio, Pennsylvania, Rhode Island, and Connecticut. Primary threats to Kentucky yellowwood include forest management practices, disease, non-native invasive plants, and pests. Amur honeysuckle is the main non-native plant that threatens this species (NatureServe 2019).

In Illinois, Kentucky yellowwood was reported from Gallatin County over 40 years ago, but that population (a single tree) has not been relocated since (Herkert & Ebinger). It was discovered in 1928 in Alexander County at Wolf Creek Botanical Area and, more recently, at a couple of sites on private property near there. Abundant flowering occurs only every second or third year at Wolf Creek. This population has been identified as being infected with Botryosphaeria dothidea and has less than 100 individuals. According to reports, the trees were once more numerous and grew large enough to be cut for timber. Today they are generally in poor condition; many are dead or dying, with live basal sprouts. These observations have been documented since the early 1970’s. Also, Amur honeysuckle is found throughout the Alexander County sites and could easily out-compete the Kentucky yellowwood. 29. Finger Dogshade (Cynosciadium digitatum) Finger dogshade is an annual (or perennial) herb whose stems grow 20-80 cm tall. Its range is Mississippi to Texas, north to southern Illinois and Oklahoma (Herkert & Ebinger 2002). It occurs in swamps, floodplain forests, and flatwoods (Godfrey & Wooten 1981) and reaches its northern range limit in southern Illinois. In Illinois it is found in pin oak flatwoods and adjacent disturbed areas (Herkert & Ebinger), where it blooms from May to June (Mohlenbrock 2014).

The Nature Conservancy assigned this species the Global Ranking of G4G5 in 1985. It is ranked critically imperiled in Illinois, imperiled in Missouri, and apparently secure in Mississippi. It is not ranked or is under review in Texas, Oklahoma, Arkansas, Louisiana, Tennessee, and Alabama. Threats to this species include the destruction of its native wetlands (NatureServe 2019).

In Illinois, finger dogshade is found only on Forest Service land in Jackson County. Originally collected in 1969 (Herkert & Ebinger 2002), this species was rediscovered during botanical surveys conducted at Oakwood Bottoms in 1993 by Rick Phillipe. Several populations were identified in or near ditches, levees, and rights-of-way. The largest population occurs in a railroad right-of-way. John White was unable to relocate two of the populations in 2013. Shannan Sharp was unable to relocate a couple of locations of this species in 2014, but Rick Phillipe observed one site in 2015, while Chris Benda relocated another in 2018 and found that the population had expanded. Non-native invasive species have not been yet been documented at these sites, but it Oakwood Bottoms has many non-native invasive plants, which are brought in by waterfall and from the levees and waterways there. 30. Manyflower Flatsedge (Cyperus lancastriensis) Manyflower flatsedge is a perennial, rhizomatous sedge, found primarily in the southeastern United States. In Illinois, its habitat is described as moist, usually sandy woods (Herkert & Ebinger 2002). In

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Illinois it flowers from August through October (Mohlenbrock 2014). It is rarely encountered but found in moist, sandy woods of Massac, Pope and Pulaski Counties. It is also known from a little north in Perry County.

Manyflower flatsedge was given the Global Heritage Status Rank of G5 in 1984. It is listed as critically imperiled in Delaware, Illinois (endangered), and New Jersey; imperiled in the District of Columbia and Pennsylvania: vulnerable in Georgia, Kentucky, North Carolina, and West Virginia; apparently secure in Mississippi; and secure in Virginia. It is not ranked or is under review in the remaining states where it has been found (NatureServe 2018).

Manyflower flatsedge has been found in Massac, Perry, Pope, and Pulaski. On the Forest, Elizabeth Shimp collected this species at the Golconda Job Corps in Pope County on July 23, 1996. John Schwegman has reported it near the Ohio River. It many have been found at other sites on the Forest, but it is unclear where they are. The future of the Golconda Job Corps population is uncertain since the property is up for trade, sale, or release from the Shawnee National Forest. This sedge at this location could be threatened by nearby infestations of garlic mustard and Nepalese browntop. 31. Greater Yellow Lady’s Slipper (Cypripedium parviflorum var. pubescens) Greater yellow lady’s slipper is a rhizomatous, perennial orchid found in most of the United States and adjacent Canada (NatureServe 2017). In Illinois it is found in both dry and moist open woodlands and although not common, is found scattered throughout the state (Mohlenbrock 2014).

The Nature Conservancy assigned greater yellow lady’s slipper the Global Heritage Status Rank of G5T5 in 2002. It is ranked critically imperiled in Idaho, Arizona, Delaware, Maryland, Utah, and Rhode Island; imperiled in New Hampshire, Mississippi, Wyoming, New Mexico, North Dakota and in 3 Canadian provinces; and vulnerable Illinois, Indiana, North Carolina, Alabama, South Carolina, New York, Vermont and 4 Canadian provinces. It is apparently secure in Ohio, Pennsylvania, West Virginia, Kentucky, Virginia, and New Brunswick, Canada, and secure in 2 Canadian provinces. It is currently not ranked or is under review in 18 states and 1 Canadian province (NatureServe 2017).

Greater yellow lady’s slipper has been historically documented from 52 Illinois counties. In southern Illinois, it has been found in Alexander, Jackson, Johnson, Massac, Pope, Pulaski, Union, and Williamson Counties, where it is considered rare with few individuals within a population reaching the flowering stage. Populations on the Shawnee National Forest are generally less than a dozen individuals each. Known populations on the Forest have been dug up by orchid enthusiasts for their beauty, becoming extirpated from their native habitats.

On the Forest, greater yellow lady’s slipper has been found primarily at unprotected sites. In Alexander County it was collected from Ozark Hill Prairie Research Natural Area by Rick Phillippe on April 30, 1992. In Gallatin County, Elizabeth Shimp found it at Thacker Hollow in July and September 2009. Chris Benda found this species at ten sites in the Kinkaid Lake area in Jackson County from July to October 2019. Mark Basinger and Ms. Shimp found this orchid on July 2009 in Pope County at Lusk Creek Canyon Ecological Area on an oak-hickory wooded slope. Ms. Shimp found it recently in Union County at the Hamburg Hill area on October 6, 2014. This species has become increasingly hard to find in its past known locations. Non-native species that could threaten this species are Nepalese browntop, Japanese honeysuckle, Amur honeysuckle, autumn olive, and multiflora rose.

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32. Eastern Hay-scented Fern (Dennstaedtia punctilobula) Eastern hay-scented fern is an arching perennial fern that occurs in the eastern United States and adjacent Canada. In Illinois this species is restricted to Johnson and Pope Counties, primarily within the Shawnee National Forest, on moist, north-facing sandstone ledges. These ledges vary in length from a few inches to several hundred feet, and sphagnum mosses are typical associates.

The Nature Conservancy assigned this species the Global Ranking of G5 in 1984 (last reviewed in 2011). Its Conservation Status is critically imperiled in Michigan and Newfoundland, Canada; imperiled in Illinois, Missouri, and Arkansas; vulnerable in Indiana and Alabama; apparently secure in Kentucky, and secure in North Carolina, West Virginia, Virginia, Delaware, New Jersey, New York, and Ontario, Quebec, New Brunswick, Nova Scotia, and Prince Edward Island, Canada. It is not ranked or under review in 14 states (NatureServe 2017).

Eastern hay-scented fern is known from Johnson and Pope Counties in southern Illinois and was recently found in Ogle County west of Chicago. Most recorded occurrences are located on the Shawnee National Forest. It was found at Bell Smith Springs Ecological Area, Double Branch Hole Ecological Area, Hayes Creek/Fox Den Ecological Area, and Lusk Creek Wilderness in Pope County. An occurrence at Massac Tower Ecological Area in Pope County is probably a mis-identification. This fern has also been documented at a state nature park in Johnson County and at state nature preserve in Pope County.

A few years ago, it was documented that Nepalese browntop had taken over the bluff top at Secret Canyon in Lusk Creek Wilderness. This non-native invasive grass was starting to cover the cliff face where a population of eastern hay-scented fern is located. It would be beneficial to control or eradicate the Nepalese browntop before it completely replaces the fern. A selective herbicide for grasses could save the fern from becoming extirpated at this site. 33. Variable Panic Grass, Joor’s Panic Grass (Dichanthelium joorii) Joor’s panic grass is a tufted, warm-season perennial grass with decumbent culms found in floodplain and swamp forests of the southeastern United States. This species ranges from Texas and Florida in the south to Illinois, Michigan, New York and Maine in the north (Hill 2007af. The southern Illinois populations are disjunct from its normal range by over 300 miles (Herkert & Ebinger 2002), where it is found in low swamps and floodplain forests (Hill 2007f). It flowers and bears fruit from June to October (Mohlenbrock 2014). Some botanists consider it a synonym of a broadly defined Dichanthelium commutatum, but in Illinois it is considered a distinct species (Hill 2007f).

The Nature Conservancy assigned this plant a Global Ranking of G5 in 1994 (G5 as D. commutatum in 1988; NatureServe), but it is listed as endangered in Illinois (Herkert & Ebinger). Threats to this plant are not listed in the available literature. But because this plant grows in bottomlands, swamps, and other wetland habitat, its primary threats are likely the loss of wetlands and the disruption of historic, hydrologic cycles (Hill 2007f).

In southern Illinois it is known from floodplain forests in Johnson and Union counties. It has been collected from the floodplain forest at LaRue-Pine Hills/Otter Pond Research Natural Area in Union County, Bell Pond inside of Grantsburg Swamp Ecological Area (Johnson County) and the state-managed Little Black Slough/Heron Pond along the Cache River in Johnson County. It was found in Massac County in 952, although the location is uncertain. Little information is available on population trends for this

xix plant in Illinois. Since this grass has been collected at few locations in Illinois, and those locations are at protected sites, it is likely that its populations are remaining stable. 34. Ravenel’s Rosette Grass (Dichanthelium ravenelii) Ravenel’s rosette grass is a loosely tufted, warm-season, perennial grass. It has been found in the southeastern and south central United States, with southern Illinois at the northern edge of its range. In Illinois this grass grows in dry, open forests on rocky ledges, usually in light shade on acidic soils (Hill 2007g). Flowers and fruits are produced from June through September (Mohlenbrock 2014).

Ravenel’s rosette grass was assigned the Global Rank of G5 by The Nature Conservancy in 1984. It is listed as vulnerable in Maryland, North Carolina, and Virginia; imperiled in Delaware; and critically imperiled in Illinois. It is not ranked or is under review in 13 states and the District of Columbia (NatureServe). Ravenel’s rosette grass is a fire dependent species, so its main threat is fire suppression. Other threats include canopy closure from succession, clear-cutting, herbivory, grazing, user created trails (equestrian, in particular), invasive plant encroachment, and habitat loss from development (Hill 2007g).

In Illinois Ravenel’s rosette grass has been found in Hardin, Pope, Saline, and Union Counties. It has been located at several sites on the Forest. There was an occurrence at Atwood Ridge Research Natural Area in Union County. However, it has not been seen there since 1977. In Hardin County it has been found at a site north of Lamb by Rick Phillipe on June 16, 1988. However, John White did not find this grass there on June 20, 2005; the road along which it was located had been widened and invaded by Nepalese browntop. Other Hardin County sites where this grass was found are Battery Rock Road (Mark Basinger on July 18, 1998; last observed on July 13, 2002 by Chuck Walker) and Barker Bluff Research Natural Area (Mark Basinger and Jody Shimp on July 31, 1998; last observed by Mark Basinger on June 6, 2008). In Pope County it was found at Dog Creek Barrens Ecological Area by Mark Basinger on July 9, 2004 (another site invaded by Nepalese browntop) and at Burden Fall Wilderness by Chris Benda and Josh Wibbenmeyer on June 16, 2009. 35. Yadkin’s Panic Grass (Dichanthelium yadkinense) Yadkin’s panic grass is a perennial grass of the southeastern United States (Hill 2007i). It occurs in sandy soil of mesic forests and gravelly streambanks in Illinois (Herkert & Ebinger 2002), where it blooms and bears fruit from May to September (Mohlenbrock 2014).

A Global Heritage Status Rank has not been determined for Yadkin’s panic grass. In Illinois this grass is listed as endangered (Herkert & Ebinger 2002). On the Forest, the primary threats for this grass is user- developed hiker/equestrian trails, clear-cutting, grazing, exotic plant species, and loss of habitat from changes in hydrology. Clear-cutting in floodplain or swamp forest that dries out the understory may also be threat, as well as herbicide treatment along powerline clearings (Hill 2007i).

Yadkin’s panic grass has been found in Gallatin, Johnson, and Pope Counties in Illinois. The Johnson County occurrence is historical (Herkert & Ebinger 2002). In Gallatin County Chris Benda and Mark Basinger found it at Camp Cadiz October 17, 2008. The remaining occurrences of this grass are in Pope County. On the Forest this grass has been found at Gyp Williams Hollow Ecological Area, Jackson Hole Ecological Area, Bell Smith Springs Ecological Area, Cretaceous Hills Ecological Area, Massac Tower Springs Ecological Area, Jackson Hole Ecological Area, Lusk Creek Canyon Ecological Area, Lusk Creek Canyon Zoological Area, Lusk Creek Wilderness Area, Double Branch Hole Ecological Area, and within the

Snow Springs Ecological Area (reported in 1969, seep springs). Yadkin’s panic grass has also been found at a state natural area in Pope County. Almost all of these sites are threatened by Nepalese browntop. Yadkin’s panic grass could easily be displaced by this non-native invasive grass if is not controlled. At the Lusk Creek Wilderness site, success with controlling Chinese yam has been made at some of its locations; controlling the Nepalese browntop would help the Yadkin’s panic grass succeed in its native habitat. 36. Eastern Leatherwood (Dirca palustris) Eastern leatherwood is a shrub from the Thymelaeaceae family. In Illinois it grows in rich, shaded woods and is uncommon to rare throughout the state. It blooms from April to May (Mohlenbrock 2014).

The Nature Conservancy assigned this species the G4 Global Rank in 1986. It is listed as presumed extirpated in the District of Columbia; critically imperiled in Delaware, Louisiana, North Dakota, and Oklahoma, as well as in Nova Scotia, Canada; imperiled in Florida, Maryland, Mississippi, New Jersey, and South Carolina, as well as in New Brunswick, Canada; vulnerable in Georgia, Iowa, and North Carolina; apparently secure in Alabama, Kentucky, Virginia, and West Virginia, as well as in Ontario and Quebec, Canada; and secure in New York. It is currently not ranked or under review in Arkansas, Connecticut, Illinois, Indiana, Maine, Massachusetts, Michigan, Minnesota, Missouri, New Hampshire, Ohio, Pennsylvania, Tennessee, and Vermont (NatureServe 2017).

It is known from a few northern counties and only from Jackson, Johnson, and Pope Counties in southern Illinois. In Pope County it is known from Millstone Bluff Ecological Area (first found by J. Schopf 1931); on a trail to Indian Kitchen in Lusk Creek Wilderness by M. Basinger 2011; and Bell Smith Springs (H.E. Ahles in 1953). 37. French’s Shootingstar (Dodecatheon frenchii) French’s shootingstar is a perennial herb known from Illinois, Indiana, Missouri, Kentucky, Arkansas, and Alabama. It is found in close association to sandstone ledges, overhangs and bluffs, preferring north and east-facing exposures. French's shooting-star grows in habitats which yield little competition from other plant species, often growing alone in bare soil. It is documented from a 10-mile wide belt in southern Illinois in six counties, all within the Greater Shawnee Hills Section of the Shawnee Hills Natural Division Hill 2002b). Generally, it blooms from April to May (Mohlenbrock 2014).

The Nature Conservancy assigned French’s shootingstar the Global Heritage Status Rank of G3? in 2018. It is listed as critically imperiled in Missouri and Alabama; imperiled in Illinois, Indiana, and Arkansas; and vulnerable in Kentucky (NatureServe 2017). Primary threats to French’s shootingstar have been unregulated recreational use under sandstone overhangs, disturbances caused by artifact hunters, and other recreational activities such as rock climbing, ATV and equestrian use, and camping/campfires. Clear cutting and other logging have also been threats when populations have been inadequately buffered. These populations are currently not threatened with extirpation because of habitat loss, but without protection of the forest, as well as sandstone ledges and shelters, these populations may decrease or might eventually be eliminated (Hill 2002b).

In Illinois, French’s shootingstar is found within Hardin, Jackson, Johnson, Saline, Pope, Union, and Williamson Counties. It was first found by Southern Illinois University Professor George Hazen French in 1871. John Voigt, Julius Swayne and William Bailey searched and found the majority of the populations in southern Illinois. It is known to occur within several areas on the Forest including Lusk Creek Canyon

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Ecological Area, Lusk Creek Canyon Zoological Area, Lusk Creek Canyon Wilderness Area, Jackson Hole Ecological Area (sandstone overhang, although it has not been relocated at this site for several years), Jackson Hollow Ecological Area (first documented by Franklin Buser on May 4, 1955), Jackson Falls Dispersed Recreation Area (first documented by Elizabeth Shimp in 2003), Bulge Hole Ecological Area, Little Grand Canyon/Horseshoe Bluff Ecological Area, Garden of the Gods Ecological Area, Schwegman Ecological Area (threatened by Nepalese browntop), Bell Smith Springs Ecological Area (base of bluff in mesic upland forest), and Double Branch Hole Ecological Area.

During 2002, these populations were not threatened with extirpation because of habitat loss. However, without protecting the forest and sandstone ledges and shelters that this species is dependent on, these populations could eventually become decreased or eliminated (Hill 2002b). Several sites of French’s shootingstar were visited over the last few years. Many of the sites have become over-run with Nepalese browntop and vines of Japanese honeysuckle have been moving down the bluffs to the populations. This project would have beneficial impacts to this species if these two non-native species were controlled at these locations. 38. Goldie’s Woodfern (Dryopteris goldieana) Goldie’s woodfern is a short-creeping, scaly fern with fronds up to 1 meter in length (Mohlenbrock 1999). Its range is from New Brunswick to Ontario, south to Iowa, Tennessee, and North Carolina (NatureServe). In Illinois it grows in moist, shaded woodlands (Mohlenbrock 1999).

Goldie’s woodfern has been given a Global Heritage Status Rank of G4G5 by The Nature Conservancy in 2011 because of its status range-wide. It is critically imperiled in Arkansas, Alabama, Delaware, and South Carolina; imperiled in Iowa, Missouri, New Hampshire, Maryland, and Maine; and vulnerable in Minnesota, Georgia, North Carolina, New Jersey, Connecticut, Massachusetts, Illinois, and Quebec and New Brunswick, Canada. It is also listed as apparently secure in Ontario, Canada, Kentucky, West Virginia, Virginia, Vermont, and New York, and not ranked or under review in Wisconsin, Michigan, Indiana, Ohio, Pennsylvania, Rhode Island, and the District of Columbia. Threats range-wide include logging, development and agriculture (NatureServe 2017).

This fern has been found in scattered counties in Illinois. In southern Illinois it has recorded occurrences in Jackson, Johnson, Pope, Union, and Williamson Counties (USDA, NRCS). On the Shawnee National Forest, this plant has been located within Lusk Creek Wilderness and south of Copperous Branch Limestone Barrens Ecological Area along Lusk Creek in Pope County. It has also been found in Hardin County along the Ohio River. Several locations are known from Williamson County on US Fish and Wildlife Service lands. 39. Wolf’s Spikerush (Eleocharis wolfii) Wolf’s spikerush is perennial, mat-forming sedge that grows in marshes, swamps, wet prairies and other wetland habitats. Its range is the eastern and central United States and Saskatchewan, Canada (NatureServe 2018). In Illinois, this species habitat is described as “wet ground”, where it flowers from May to July (Mohlenbrock 2014). In shaded sites, plants may become decumbent and abort before reaching maturity; this species appears to require adequate light to become fertile. In southern Illinois it has been found in pin oak flatwoods around ephemeral pools or wet ditches that have open canopies (Phillippe 2004b).

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The primary threat to Wolf’s spikerush is the loss of its native wetland and grassland habitats from drainage and alteration of wet areas for agriculture, development, and grazing. Indiscriminate herbicide application along railroad and highway rights-of-way also threatens this sedge. This sedge requires high levels of light to produce seed, so woody and invasive plant encroachment in areas where historic fire regimes are now absent have substantially reduced its habitat (NatureServe 2018, and Phillipe 2004b).

The Nature Conservancy ranked this species G3G5 in 2013 (NatureServe). It is listed as critically imperiled in Iowa, Wisconsin, Minnesota, Ohio, Virginia, Tennessee, Georgia, Alabama, Kansas, and Texas; imperiled in Indiana and Nebraska; and vulnerable in Arkansas, Missouri, and Louisiana. It is possibly extirpated in North Dakota and Oklahoma and listed as introduced (exotic) in New York. It is not ranked or under review in Mississippi, and Saskatchewan, Canada (NatureServe). It is not listed in the state of Illinois.

In Illinois there are records of Wolf’s spikerush from 20 counties, but only 15 counties are known to have extant populations. Of 41 discrete extant populations, 7 are known from Forest Service managed lands (Phillippe 2004b). Southern Illinois locations of this sedge outside the Forest are on private land in a flatwoods near Equality in Gallatin County (June 29, 1992), in flatwoods at Mermet Swamp State Nature Preserve in Massac County (May 28, 1992), at unknown locations in Pope County; and in flatwoods northeast of Harrisburg on private land in Saline County (June 5, 1956 and re-vouchered May 27, 1992). On Forest land it has been found at several sites at Oakwood Bottoms in Jackson County (collections by Rick Phillippe May 4, 5, and 6, 1993) and in a floodplain forest at LaRue-Pine Hills/Otter Pond Research Natural Area in Union County. 40. Creeping Eryngo (Eryngium prostratum) Creeping eryngo is a prostrate perennial herb found in the southeastern United States. It reaches its northern range limit in the southern tip of Illinois (Herkert & Ebinger). Across its range it grows in lake margins, depressions, swamps, and wet woodlands (Godfrey & Wooten 1981). In Illinois, this herb has been found along muddy and sandy shores, as well as at artificial impoundments on the Shawnee National Forest (Herkert & Ebinger 2002). It flowers and bears fruit from May to November (Mohlenbrock 2014).

Creeping eryngo was given the Global Heritage Status Rank of G5 in 1985. It is listed as critically imperiled in Illinois and Kansas; vulnerable in North Carolina; apparently secure in Kentucky; and exotic in Delaware and Virginia. It is listed as not ranked or under review in the remaining states where it is found (NatureServe 2018).

This species is known from Horseshoe Lake Conservation Area (Mark Basinger #5739, June 19, 1993) in Alexander County, from Teal Pond in Pope County since before 1978, and in Williamson County at Cambria Neck, Crab Orchard Lake, growing in open along path about 3 meters from the shoreline of the lake (Tatina and Don Ugent, July, 18, 1974). The non-native invasive grass, Nepalese browntop, is expanding to the site from the roadway and along the fisherman’s path around the pond. 41. Hyssopleaf Thoroughwort (Eupatorium hyssopifolium var. hyssopifolium) Hyssopleaf thoroughwort is a perennial herb in the aster family. It has been found primarily in the southeastern United States, as well as in several northeastern states along the Atlantic coast (NatureServe 2017). It grows in dry, open disturbed areas (FNA 2006), especially in dry, sandy soil

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(Herkert & Ebinger 2002). It blooms and bears fruit from August to October in Illinois (Mohlenbrock 2014).

Hyssopleaf thoroughwort was assigned the Global Ranking of G5T5 in 1988. It is listed as critically imperiled in Illinois (endangered), Ohio, and West Virginia; vulnerable in Arkansas, Kentucky, and New York; and secure in New Jersey, North Carolina, and Virginia. It is not ranked or is currently under review in the remaining states where it has been found (NatureServe 2017).

Hyssopleaf thoroughwort has been found in Illinois two counties in the extreme southern part of the state. It is currently known from one location in southern Illinois in an open sandstone barrens and adjacent open woods at Dean East Ecological Area (collected by Lawrence Stritch in 1991 and annotated by Mark Basinger) in Pope County. A second location was reported along a state highway/interstate in Johnson County (Eric Ulaszek on August 2, 1994). The Dean East site is threatened by amur honeysuckle, Japanese honeysuckle, multiflora rose, autumn olive and Nepalese browntop. 42. Plain Gentian (Gentiana alba) Plain gentian is a stout perennial herb that is found in the eastern United and adjacent Canada (NatureServe 2018). In southern Illinois it has been found in mesic barrens remnants and open upland forests. It generally flowers from mid-August through October (Mohlenbrock 2014).

The Nature Conservancy assigned plain gentian the Global Ranking of G4 in 1984. It is listed as possibly extirpated in North Carolina and Pennsylvania; critically imperiled in Kentucky, Michigan, Nebraska, Oklahoma, West Virginia, and Ontario, Canada; imperiled in Indiana, Kansas, and Ohio; and apparently secure in Wisconsin. It is not ranked or is currently under review in the remaining states where it has been found, including Illinois (NatureServe 2018). A threat to plain gentian populations are loss of native vegetation to exotic cool season grasses (Heikens 2002). Other threats to this species include fire suppression, canopy closure in open forests and barrens (USDA FS 2005), land use conversion, habitat fragmentation, and forest management practices (NatureServe).

Plain gentian is widespread across most of Illinois but has been found in only four counties in extreme southern Illinois—Alexander, Jackson, Massac, and Pope (USDA, NRCS 2020). On the Forest it is known from the mesic barrens of Burke Branch Research Natural Area in Pope County and on the lower slope of Ozark Hill Prairie Research Natural Area in Alexander County (collected by Rick Phillippe September 15, 1992). 43. Arkansas Mannagrass (Glyceria striata) Arkansas mannagrass is a perennial grass reaching (Mohlenbrock 2014) found in the lower central and eastern United States (USDA, NRCS), reaching its northwestern range limit in southern Illinois. In Illinois, it grows in shallow water, marshy soil, and swamp meadows (Herkert & Ebinger 2002). This species flowers from May through June (Mohlenbrock 2014).

The Nature Conservancy assigned this species the Global Ranking of G5 in 1989. It is listed as critically imperiled in Illinois and Oklahoma; imperiled in Mississippi; and apparently secure in Kentucky. It is not ranked or is currently under review in Tennessee, Missouri, Arkansas, Louisiana, and Texas (NatureServe 2017).

In southern Illinois, the primary threat to Arkansas mannagrass is loss of its wetland habitat. This grass occurs in isolated patches within the swamps. Opportunities for seed dispersal are limited because of

xxiv reduced numbers of protected swamps and permanent wetlands. This species requires high-quality conditions without chemical pollution. It also requires wetland habitat without hydrologic alterations, such as water drainage (USDA FS 2005).

In Illinois, there are reports Arkansas mannagrass it occurs in Alexander, Jackson, Johnson, and Union counties. The Alexander County locations (roadside swamp; one clump at one site; “clumps” at second site) were found by Steve Hill on June 23, 1999 and May 3, 2000 within ¼ mile from each other, and another site at Clear Creek Swamp Ecological Area was discovered May 24, 2007 by John White. In Jackson County it was found at Oakwood Bottoms (bottomland woods; about 50 plants) by Rick Phillippe on May 27, 1993, and a separate Jackson County location is known from Cave Valley near Pomona Natural Bridge (Tom Sadowski on May 22, 1981). There was no information regarding the Johnson County report at the time of this writing. In Union County this grass collected at LaRue swamp in 1940 (unknown collector); then subsequent collections were made by Franklin Buser at LaRue-Pine Hills/Otter on June 24, 1956 (then later collections at LaRue were made by Robert Evers on May 21, 1957 and May 22, 1969). Steven Hill and Jason Koontz found 2 nearby sites in Union County near Ware on May 2001. 44. Swamp Sunflower (Helianthus angustifolius) Swamp sunflower is a perennial sunflower (Mohlenbrock 2014). It is primarily a coastal plain species of the United States but is found farther north from New York to Illinois (NatureServe 2018). In Illinois it is found in a variety of habitats, including flatwoods, old fields, seeps, and roadsides (Herkert & Ebinger 2002), where it flowers from August to October (Mohlenbrock 2014).

The Nature Conservancy assigned this plant the Global Ranking of G5 in 1985. It is listed as critically imperiled in Indiana; imperiled in Illinois, Missouri, and New York; vulnerable in Delaware; apparently secure in Kentucky, New Jersey, and Virginia; secure in North Carolina; and extirpated in Pennsylvania. It is unranked or under review in the remaining states where it is found, except for West Virginia, where it is ranked as exotic (NatureServe 2018).

In Illinois swamp sunflower has been found in Massac, Pope, Pulaski, and Wayne Counties (Mohlenbrock 2019). Robert Evers collected this species in Massac County (October 23, 1957 and October 4, 1972) and in Pope County (September 29, 1965). One of the Massac County locations is on state land at the Mermet Conservation Area (found by Don Kurz in 1965 and John Voigt September 28, 1965). Another site is just north of Massac Forest Nature Preserve and appears to be on private property. This plant was also found in Pope County on state land at Cretaceous Hills Nature Preserve (person unknown) in 1987. In Pulaski County this species was found near Perks by Robert Evers (October 4, 1972) and later in the Cache River State Natural Area by Kevin Winshap (September 18, 1989). On the Forest, it was documented at Pope County on the edges of a seep spring at Dean Cemetery West Ecological Area by John Schwegman on September 13, 1968; by Lawrence Stritch at an intermittent stream drainage near an abandoned road at Dean Cemetery East Ecological Area (on September 1, 1991); and by John Schwegman at Kickasola Cemetery Ecological Area in a seep spring (1969). 45. Kidneyleaf Mudplantain (Heteranthera reniformis) Kidneyleaf mudplantain is a low growing, perennial herb with creeping rhizomes. It grows in muddy soil or shallow water (Mohlenbrock 2014). This plant is found primarily in tropical South America and Central America, but also grows in Mexico and the eastern and central United States (NatureServe).

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Illinois is at the northern limit of its range (Herkert & Ebinger), where it flowers in July and August (Mohlenbrock 2014).

The Nature Conservancy has given kidneyleaf mudplantain the Global Heritage Status Rank of G5 (1994) because this species is not threatened globally. It is possibly extirpated in Connecticut; critically imperiled in Illinois, Iowa, Ohio, South Carolina, and West Virginia; imperiled in North Carolina, and vulnerable in New York and Georgia. It is apparently secure in Kentucky, Virginia, New Jersey, and Delaware. It is not ranked or is currently under review in 12 states. At the periphery of its range, the primary threat to this species is the loss of its wetland habitat, especially by permanent hydrological alteration. But fluctuating water levels, especially from beaver dams, can give this plant an advantage over other wetland species. Shading and subsequent competition from other plants is another threat. Invasive plants, including RCG and Phragmites, can out-compete this herb. Cold temperatures may also limit the range of this tropical species (NatureServe 2018).

In southern Illinois kidneyleaf mudplantain has been found in Alexander, Pope, and Union Counties. Slightly north it has been found in St. Clair, Lawrence, and Wabash Counties. On the Forest it is known from LaRue Swamp at LaRue-Pine Hills/Otter Pond Research Natural Area in Union County, where it was last observed in 1977. It was also found on private land near Ware Union County in 2001 but was not observed during a 2013 search. A population was found in 1977 and 1990 at Homberg Spring (private) in Pope County; it has not found in subsequent searches. Another population was found near Tamms in Alexander County by Steven Hill on August 13, 1999. It was also found at Horseshoe Lake in Alexander County in 2004. 46. Spiked Crested Coralroot (Hexalectris spicata) Spiked crested coralroot is a rhizomatous, perennial orchid found in the southeastern, south central, and southwestern United States, as well as in northern Mexico (Hill 2007b). In Illinois it is found in dry, calcareous woods and dry prairie openings, primarily along the Mississippi River bluffs and on limestone glades within the Shawnee National Forest (Herkert & Ebinger 2002). This species grows in dry, sunny limestone habitats where competition from other plants is minimal. It occurs in some of the natural areas in southern Illinois that have been prescribed burned (USDA FS 2005). This orchid flowers from June to September (Mohlenbrock 2014).

The Nature Conservancy gave spiked crested coralroot the Global Heritage Status Rank of G5 in 1999. It is ranked possibly extirpated in Maryland; critically imperiled in Illinois, Oklahoma, and West Virginia; and imperiled in Arkansas, Indiana, Louisiana, Mississippi, New Mexico, and North Carolina. It is considered vulnerable in Alabama, Arizona, Florida, Georgia, Ohio, and Virginia. It is either not ranked or under review in South Carolina, Tennessee, Missouri, Texas, and Kansas. It is ranked apparently secure in Kentucky (NatureServe).

It is somewhat surprising that spiked crested coralroot is considered secure globally because it is recognized as rare in so many states. The primary threat to this species is its habitat loss and fragmentation from recreation, logging, the absence of fire, herbivory and grazing, and the conversion of forests for construction, agriculture, quarrying and mining (Hill 2007b). On the Shawnee National Forest, some of the glades where this species occur are threatened by being taken over by autumn olive and amur honeysuckle. These sites are being invaded by these aggressive non-native invasive plants at an alarming rate (Elizabeth Longo, personal observations).

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In southern Illinois, spiked crested coralroot is historically known from Hardin, Jackson and Pope Counties. It is known also from the nearby counties of Randolph and Monroe. The Fountain Bluff population in Jackson County has not been seen since 1974, and the Jackson Hollow Ecological Area population in Pope County has not been seen since 1950 (Raymond Hatcher). The Whoopie Cat Mountain Research Natural Area (RNA) population in Hardin County was seen in 2008 where at least 16 plants were found, then again observed in 2017 by Christopher Benda. In 1989 (Todd Fink), 13 plants appeared in the Whoopie Cat RNA dry woodland following a prescribed burn (it was first discovered in 1976 by Don Kurz with 29 plants but not seen again until 1989). On July 30, 2019 Jody Shimp, Nick Seaton, David Barfknecht, and Ava Alford found 5 plants that came up at this site. The Barker Bluff Research Natural Area population was discovered in 1993 with 17 plants (Jody Shimp) and relocated in 1994 with 8 plants (Jody Shimp on October 10, 1994). The Jackson County siting was in August of 1974 by Don Kurz just SE of the Fountain Bluff Station. It has not been relocated at this site. There is an unconfirmed report of this species occurring at Leisure City Barrens Ecological Area in Pope County. On August 1, 2019, Jody Shimp, Seaton, Barfknecht, and Alford found 30 plants on the Flick Hill State Nature Preserve on private property in Pope County. 47. American Featherfoil (Hottonia inflata) American featherfoil is an aquatic winter annual that occurs in quiet water of swamps and permanently wet ditches from Maine west to Illinois and Missouri and south to Texas and Georgia. This species germinates and grows in the fall and develops in the winter protected under the water, then reaches the water’s surface and flowers in the spring (NatureServe 2017). According to Mohlenbrock (2014), it blooms from June to August in southern Illinois, but NatureServe (2017) states it decays from mid-June to August depending on its location.

The Nature Conservancy assigned this species a rank of G4 in 1994. It is currently listed as presumed extirpated in Pennsylvania; possibly extirpated in Ohio; critically imperiled in West Virginia, Maine, Rhode Island, New Jersey, Maryland, Georgia, South Carolina, North Carolina, New Hampshire, and Mississippi; imperiled in Illinois, Missouri, Indiana, Oklahoma, Tennessee, New York, Delaware, and Alabama; and vulnerable in Connecticut, Massachusetts, Virginia and Texas. This species is apparently secure in Kentucky, and either not ranked or under review in Arkansas, Louisiana, and Florida (NatureServe 2017).

The primary threats to American featherfoil are the loss/conversion of wetlands, alteration of hydrology and deteriorating water quality. Invasive species, severe floods and removal of beaver populations are also listed as threats to this plant. American featherfoil populations are in decline over much of its range. Populations in southern Illinois currently appear to be stable as most locations are protected, but many of the primary threats to this species including exotic species encroachment, severe fluctuations in water levels, wetland drainage and siltation remain a threat (NatureServe 2017).

In southern Illinois American featherfoil has been recorded from Jackson, Johnson, Saline, and Union Counties. It has been collected on the Forest from several sites at Cave Valley (Silvey Pond) in Jackson County. In Union County it was found at LaRue-Pine Hills/Otter Pond Research Natural Area (pool of water at base of cliff, LaRue Swamp, and Winter’s Pond) and in a swamp just east of Atwood Ridge. It has been found off the Forest in Johnson County at Heron Pond, Little Black Slough and on private land near West Vienna; at Round Pond in Pope County; on private land near Carrier Mills in Saline County; and near Ware in Union County.

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48. Rock Clubmoss (Huperzia porophila) Rock clubmoss is a perennial, evergreen clubmoss. It is found in the eastern United States and Canada (NatureServe 2017). Across its range, this species grows primarily on damp, shaded, acidic sandstone (FNA 1993), although it has occasionally been found on limestone (NatureServe 2017). In Illinois it grows on moist, shaded, acidic sandstone cliffs (Nÿboer & Ebinger 2004), producing spores from June to September (Mohlenbrock 2014).

Rock clubmoss was given a Global Heritage Status Rank of G4 by The Nature Conservancy in 1990. It is listed as presumed extirpated in Maryland; critically imperiled in Alabama, Georgia, Iowa, Pennsylvania, South Carolina, Virginia, West Virginia, and Ontario, Canada; imperiled in Illinois (threatened), Minnesota, Missouri, and North Carolina; vulnerable in Indiana and Wisconsin; and apparently secure in Kentucky. It is unranked or under review in Ohio, Tennessee, and Vermont. This species is potentially threatened by trampling or rock climbing, with low level threats from highway construction and development (NatureServe 2017). On the Forest, rock clubmoss is threatened infestations of Nepalese browntop and Japanese honeysuckle (Elizabeth Longo, personal observations).

In Illinois, rock clubmoss has been recorded in four northern counties and in the southern counties of Alexander, Gallatin, Jackson, Johnson, Massac, Pope, Randolph, and Union. It was collected by Robert Evers on October 23, 1959 at Pounds Hollow Ecological Area (Gallatin County) and subsequently collected by Florence Givens and Annette Parker in 1986, then again by Loy Rick Phillippe and John Ebinger on 13 Jul 2011. Evers also collected this species at Jackson Hollow Ecological Area in Pope County on April 8, 1963 and November 13, 1963. It is also known from Lusk Creek State Nature Preserve (Mark Basinger 21 Jul 1992), Lusk Creek banks, and Lusk Creek North Ecological Area (William Bailey and Julian Swayne on October 16, 1952). It was collected at Double Branch Hole Ecological Area on April 23, 1981 by Lawrence Stritch on a mesic north facing cliff. Loy Rick Phillippe found this species at Claridy Spring north of Cedar Grove Church and Cemetery on 14 Oct 1992. Phillippe, Paul Marcum and John Ebinger collected this species at Split Rock Hollow on 14 Aug 2014, where it was known from previously. Mike Homoya first documented this species in Jackson County on a vertical rock cliff on the south bank of Big Branch on May 18, 1974. Loy Rick Phillippe collected it at Piney Creek Ravine Nature Preserve in Randolph County. There was no information for the Alexander, Massac and Union County occurrences at the time of this writing. 49. Goldenseal (Hydrastis canadensis) Goldenseal is a perennial found in eastern North America. It is best known as an herbal remedy for a variety of ailments. The core part of its range is in the Ohio River Valley in Indiana, Ohio, Kentucky and West Virginiana. It is also relatively common in Illinois and Missouri. It is found as far north as Ontario, Canada and as far south as Georgia and Alabama. It grows in rich, deciduous woodlands with good airflow and good drainage; mild disturbance often stimulates its proliferation. It flowers from April to May and produces fruit from June to July (NatureServe 2019).

The Nature Conservancy assigned goldenseal the rank of G3G4 in 2012. It is listed as critically imperiled in Connecticut, Kansas, Massachusetts, Mississippi, New Jersey, and Vermont; imperiled in Alabama, Georgia, Maryland, Michigan, New York, and Ontario, Canada; vulnerable in Delaware, Indiana, Iowa, North Carolina, Virginia, West Virginia, and Wisconsin; apparently secure in Arkansas, Illinois, Kentucky, Ohio, Pennsylvania, and Tennessee; and secure in Missouri (NatureServe 2019).

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Goldenseal is considered uncommon to secure throughout most of its range, but it been in long-term decline. It was used as an herbal remedy by indigenous people in eastern North America, and its use has increased steadily since European settlement. Although collection and harvest of wild populations has impacted populations, cultivated plants currently supply most markets, so over-collection is not its principal threat. The major threat to this species is the destruction and decline of its woodland habitat. Competition from invasive plants and deer browsing have also contributed to the decline of some populations (NatureServe 2019). It is widespread across the Shawnee National Forest, but populations are generally small. Several non-native invasive plants threaten goldenseal, with Nepalese browntop and invasive shrubs the worst invaders (Elizabeth Longo, personal observations).

Goldenseal is found in all the southern Illinois counties where the Shawnee National Forest has land and appears fairly secure. Locations where is has been found on the Forest include Ozark Hill Prairie RNA (1992) in Alexander County; Panther Hollow Research Natural Area (1995) and Lee Mine (2017) in Harding County; Cedar Lake (2015, 2015) and Kinkaid Lake (2019); Lake of Egypt (1985) and Grantsburg Swamp EA (1990) in Johnson County; Jackson Hollow EA (1987, 1997) and north of Millstone Bluff EA (2011) in Pope County; and LaRue-Pine Hills/Otter Pond RNA (1955, 1966, 1983), Bald Knob Cross Road (1988), and Atwood Ridge RNA (1955, 1988, and 1991) in Union County. 50. One-flowered False Fiddleleaf (Hydrolea uniflora) One-flowered false fiddleleaf is a decumbent perennial herb that occurs in swamps, wet shores, and roadside ditches (Godfrey & Wooten 1981). It ranges Florida and Texas then north to southern Illinois, Indiana, and Missouri (USDA, NRCS), reaching its northern range limit in southern Illinois. In Illinois, this herb is found in swamps and on wet shores (Herkert & Ebinger), flowering from June to September (Mohlenbrock 2014).

One-flowered false fiddleleaf has been given a Global Heritage Status Rank of G5 by The Nature Conservancy in 1988. This species is critically imperiled in Illinois (endangered) and Kentucky, and not ranked or under review in Indiana, Tennessee, Alabama, Mississippi, Missouri, Arkansas, Louisiana, Oklahoma, and Texas. Threats range-wide include loss of its swamp habitat from hydrological changes, reduction in water quality, woody plant encroachment from the absence of fire, and invasive plant infestations (NatureServe 2017).

In Illinois, one-flowered false fiddleleaf has been found in Alexander, Massac, Jackson, Pulaski, and Union Counties (Herkert & Ebinger 2002). On the Forest this herb has been found at LaRue-Pine Hills/Otter Pond Research Natural Area in Union County (LaRue Swamp and Winter’s Pond), a ditch along Highway 3 near Gorham in Jackson County, Grantsburg Swamp in Johnson County. Off the Forest, it was found on private property at Black Bottoms in Massac County and at a couple of sites at the Cache River State Natural Ares. The location of the sites in Alexander and Pulaski Counties was unavailable at the time this report was written. 51. Allegheny Stonecrop (Hylotelephium telephioides) Allegheny stonecrop is a succulent perennial herb that occurs in the eastern United States and adjacent Canada. It is found in dry, rocky places typically in the mountains and is disjunct in western Kentucky, southern Indiana, and southern Illinois (Nÿboer & Ebinger 2004). On the Forest, it occurs in thin soil pockets on sandstone cliffs, ledges, and slide blocks. It generally flowers in southern Illinois from August

xxix to September (Mohlenbrock 2014), however, it has been seen to flower earlier in the season (Elizabeth Longo, personal observations).

The Nature Conservancy assigned this species a rank of G4 in 1988. This species is currently listed as presumed extirpated in New Jersey, possibly extirpated in New York, imperiled in Indiana and Kentucky, and vulnerable in Pennsylvania. This species is apparently secure in West Virginia, Virginia, and North Carolina, and either not ranked or under review in Illinois, Ohio, Louisiana, South Carolina, the District of Columbia, Maryland, and Connecticut. Ontario, Canada lists this species as an exotic (NatureServe 2018). The primary threats to this species in southern Illinois are the loss of habitat because of recreational use on the cliff tops and cliff faces, and the threat of Japanese honeysuckle and Nepalese browntop that invade the cliff tops and faces (USDA FS 2005).

Allegheny stonecrop has been found in extreme southern Illinois in Gallatin, Hardin, Pope, and Saline Counties. On the Forest it has been found at several sites. In Gallatin County Chris Benda and Joshua Wibbenmeyer found new sites at Black Vulture Hollow (July 31, 2009) and Buzzard’s Point (August 4, 2009). In Hardin County Chris Benda found several plants at Pounds Hollow near Rim Rock on April 21, 2013 and on June 24, 2009 Benda and Wibbenmeyer rediscovered this species at High Knob. It has also been found in that County at Pounds Hollow where it was last seen by Chris Benda on September 27, 2018. This species was recently discovered in Jackson County by Chris Benda and Josh Wibbenmeyer on March 31, 2017 at Cover Hollow. In Pope County this plant has been found at Bell Smith Springs Ecological Area (last observed August 26, 2013), Hayes Creek Canyon/Fox Den Creek Ecological Area (last seen in 1981), at Jackson Hollow Ecological Area (last seen in 1985), and at Lusk Creek Wilderness (last seen at two sites in 2011). In Saline County this plant has been found at Garden of the Gods Wilderness (June 4, 2011 by Chris Benda), Stoneface Research Natural Area (last seen on by John Wilker August 17, 2018), and at Cave Hill Research Natural Area. This species has also been found off Forest Service lands at sites including: Cave in Rock State Park (1978) and Karbers Ridge (May 7, 1970 by Robert Evers) in Hardin County; at Lusk Creek Canyon Nature Preserve (May 27, 2011 by Chris Benda) in Pope County; and at Still House Hollow (June 1932 by H.S. Pepoon) and Wamble Mountain (October 25, 1949 by Robert Evers) in Saline County. 52. Large Whorled Pogonia (Isotria verticillata) Large whorled pogonia is a perennial orchid. It is has been found from in the eastern United States and adjacent Canada (USDA, NRCS). In Illinois this orchid has been found near seep springs and near the bottom of forested ravines (Herkert & Ebinger 2002), where it flowers in late May or early June (Mohlenbrock 2014).

The Nature Conservancy assigned large whorled pogonia a rank of G5 in 1984 (NatureServe). This species is ranked as presumed extirpated in Maine; possibly extirpated in Ontario, Canada; critically imperiled in Florida, Illinois (endangered, IESPB), Missouri, New Hampshire, and Oklahoma, as well as in Ontario, Canada; imperiled in Alabama, Michigan, North Carolina, and Vermont; vulnerable in Connecticut, Delaware, Georgia, Indiana, Louisiana, Massachusetts, Mississippi, New York, and Rhode Island; apparently secure in Kentucky and New Jersey; secure in Virginiana and West Virginia; and not ranked or under review om Arkansas, District of Columbia, Maryland, Ohio, Pennsylvania, South Carolina, and Tennessee. Although widespread, it is highly threatened by land-use conversion, habitat fragmentation, and forest management practices that allow shade-tolerant species and exotics to encroach on its habitat (NatureServe 2018).

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In Illinois, this orchid is found only in Pope County. All sites are located on the Shawnee National Forest. It has been found at several sites within Cretaceous Hills Ecological Area, as well as at a site to the east that is just outside a couple of Forest natural areas. The Cretaceous Hills sites are threatened by Nepalese browntop and Japanese honeysuckle (Basinger 2009). 53. Butternut (Juglans cinerea) Butternut is a deciduous, nut-bearing tree. It grows best on well-drained soils of bottomlands and floodplains, preferring full sunlight. Occasionally this tree is found on dry, compact, or infertile soils (Schulz 2003). Its range is the eastern half of United States and Canada (NatureServe). In Illinois, it flowers from April to May (Mohlenbrock 2014).

The Nature Conservancy assigned this species the Global Heritage Status Rank of G4 in 2006 reflecting occurrences from at least 17 states. It is listed as critically imperiled in Alabama and the District of Columbia; imperiled in Georgia, Illinois, Missouri, Mississippi, North Carolina, Kentucky, and Maryland and Ontario, Canada; and vulnerable in Minnesota, Wisconsin, Arkansas, Indiana, Michigan, West Virginia, Virginia, New Jersey, Tennessee, South Carolina, New Hampshire, Vermont, Delaware and 2 Canadian provinces. It is listed as introduced (exotic) in Washington and 2 Canadian provinces, and is either not ranked or currently under review in Iowa, Connecticut, Rhode Island, and Maine. The abundance and condition of this species are in rapid decline due to butternut canker disease, with no remedy currently. It is also threatened by competing, woody encroachment (NatureServe 2017).

Butternut is found scattered throughout the state of Illinois. It is known from all of the counties on which the Forest occurs. On the Shawnee National Forest, it is has been found at several locations. It was found in the Bean Ridge and Horse Creek Areas of Alexander County by Rick Phillipe in July 1994. In Gallatin County, it was found near Eagle Creek by Eric Ulaszek on May 25, 1995 and at Thacker Hollow by Mark Basinger and Elizabeth Longo Shimp on July 31, 2009. It was found at 4 locations in Pope County: at Burke Branch Natural Area by Elizabeth Longo Shimp; at Cretaceous Hills by Eric Ulaszek on November 2, 1995; east of Cretaceous Hills by Anna Williams on August 7, 2010; and at Jackson Hollow Ecological Area by Raymond Smith on September 20, 1986. In Union County it has been found at the LaRue-Pine Hills Research Natural Area and at Atwood Ridge Research Natural Area (May 8, 1991 by Rick Phillipe and David Ketzner). 54. Turk’s-cap Lily (Lilium superbum) Turk’s-cap lily is a bulbous, perennial herb. It is a plant often associated with wetlands or the margins of mesic upland forests. It usually grows in acidic soils (Hill 2007h). It is found in the eastern half of the United States (USDA, NRCS), with southern Illinois at the northwestern limit of its range. It grows in mesic woods and along streambanks in southern Illinois. This plant flowers from July to early August and bears fruit in September (Hill 2007h).

The Nature Conservancy has given this species the Global Heritage Status Rank of G5 (1990) because of its historically wide distribution within 26 states and the District of Columbia, but it is critically imperiled in Missouri, Arkansas, Kentucky, Louisiana, New Hampshire, and Florida. It is imperiled in Illinois and Alabama and is considered vulnerable in Indiana, Ohio, Georgia and Mississippi. This species is apparently secure in New York, New Jersey, North Carolina, and secure in Delaware, West Virginia, and Virginia. It is currently not ranked or under review in Minnesota, Tennessee, Pennsylvania, Vermont, Massachusetts, Rhode Island, Connecticut, Maryland, and District of Columbia (NatureServe 2017).

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Although Turk’s-cap lily is widespread, it is at risk at the margins of its range (Hill 2007). On the Shawnee National Forest, threats to Turk’s-cap lily include canopy closure from succession, lack of fire, and invasive plant infestations. Typically, populations do not flower, remaining in a juvenile stage because they are found in overly shaded areas. Populations on the Forest rarely produce fertile individuals. This species also benefits from prescribed burning, with plants appearing after burns takes place. Fire also reduces the threat of invasive woody plants, such as Japanese honeysuckle (USDA FS 2012).

Turk’s-cap lily is found within Alexander, Gallatin, Hardin, Jackson, Johnson, Pope, and Williamson, and Counties in Illinois. On the Forest it has been found at Ozark Hill Prairie Research Natural Area in Alexander County; near Camp Cadiz in Gallatin County; at Iron Furnace and along a tributary of Big Creek in Hardin County; north of Clear Springs Wilderness, at the Lake Kinkaid area, and along Cedar Creek in Jackson County; at Bulge Hole Ecological Area, Fink Sandstone Barrens, Simpson Township Barrens, and the east branch of Cedar Creek in Johnson County; at Bell Smith Springs, from outside the Burke Branch Research Natural Area, Hayes Creek/Fox Den Creek (mesic woodland, north-facing slope), Jackson Hollow, Lusk Creek Canyon, Lusk Creek Canyon Zoological Area, Lusk Creek Canyon Wilderness Area, and Martha’s Woods in Pope County. It has also been found near Beaver Creek, on private land near Caney Creek, at Gibbons Creek Barrens State Natural Area, on state land at Lake Murphysboro, and in US Fish & Wildlife land at Devils Kitchen Dam. 55. Limber Honeysuckle (Lonicera dioica var. glaucescens) Limber honeysuckle is a shrub-like, woody vine. Its range is difficult to determine since most botanists do not recognize the variety as distinct from Lonicera dioica. This makes its range difficult to determine. It has been reported from 17 states in the United States (centered in the Midwest) and in 7 Canadian provinces; its presence in 2 additional states has not yet been confirmed (Hill 2003d). In Illinois, this vine has been found on sandstone ledges and bluffs (Herkert & Ebinger 2002), where it blooms from May to June (Mohlenbrock 2014).

Limber honeysuckle is not recognized as a distinct taxon by the Nature Conservancy, so it has no Global Heritage Status Rank, although limber honeysuckle was ranked G5 in 1984 (NatureServe). Herbarium records in the United States indicate that the variety is most common in Wisconsin and Minnesota, with plants becoming increasingly rare proceeding south. Few states consider limber honeysuckle a legitimate variety, and only Illinois recognizes this taxon as protected (Hill 2003d), ranking it as endangered (Herkert & Ebinger 2002).

In Illinois, limber honeysuckle has only been found at only two counties. It was first discovered in Jackson County, and has been recently been found at several locations in Lake County near Lake Michigan. Both Jackson County populations occur within the Shawnee National Forest, one at the rim of a dry sandstone cliff at Fountain Bluff Station and the other at Little Grand Canyon/Horseshoe Bluff Ecological Area. Recent searches for this variety at these two locations yielded 2 separate sterile individuals, which the initial identification became questionable (Hill 2003d). Japanese honeysuckle poses the greatest threat at these locations and could easily outcompete the few individuals that are remaining.

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56. Yellow Honeysuckle (Lonicera flava) Yellow honeysuckle is a perennial woody vine found in several central and southeastern states in the United States (Hill 2003e, and USDA NRCS). Its preferred habitat is in rocky upland forests, rock bluffs, or on rocky ground near streams (Hill 2003e). In Illinois, this vine is found on forested sandstone bluffs (Herkert & Ebinger 2002), where it blooms from April to May (Mohlenbrock 2014).

The Nature Conservancy gave this species the Global Heritage Status Rank of G5? in 1984. It has been reported from twelve states: Alabama, Arkansas, Georgia, Illinois, Kansas, Kentucky, Missouri, North Carolina, Ohio, Oklahoma, South Carolina, and Tennessee. It is ranked as possibly extirpated in Ohio; critically imperiled in Illinois (endangered) and Tennessee; imperiled in Kansas and South Carolina; vulnerable in Alabama, Georgia, and North Carolina; and apparently secure in Kentucky. It is unranked or under review in Arkansas, Missouri, and Oklahoma (NatureServe 2018).

In Illinois there are confirmed reports of yellow honeysuckle in Jackson and Pope Counties, as well as an unconfirmed report in Randolph County. In Jackson County, On the Forest this plant has been found at Little Grand Canyon/Horseshoe Bluff Ecological Area, near Bear Creek Relict Botanical Area, and at Fountain Bluff (partially on private land). In Pope County, yellow honeysuckle has been found at Bell Smith Springs Ecological Area and at Lusk Creek Canyon Ecological Area. It has also been found at a state nature preserve in Pope County, and there is an unconfirmed report of it on private land from Jackson County. On the Forest, the greatest threats to yellow honeysuckle are excessive shading from fire suppression and from competition from Japanese honeysuckle. 57. Southern Crabapple (Malus angustifolia) Southern crabapple is a tall shrub or short tree that can grow to 10 meters high. It occurs in the Southeastern United States. It is a species of floodplain forests and flatwoods and reaches its northern range limit in southern Illinois (Herkert & Ebinger 2002). In Illinois it flowers during May (Mohlenbrock 2014).

Southern crabapple was given the Global Heritage Status Rank of G5? in 1984. It is listed as possibly extirpated in Ohio; critically imperiled in Illinois; imperiled in Missouri; vulnerable in Kentucky, Maryland, North Carolina, and West Virginia; and apparently secure in Virginia. It is listed as not ranked or under review in the remaining states where it has been found (NatureServe 2019). The state of Illinois lists this species as endangered (Herkert & Ebinger 2002).

Southern crabapple has been found in a few counties in Illinois in the southern part of the state. Most of these occurrences are considered historical, some from the early 1910’s and 1920’s. Illinois counties with no recent reports are Richland, Gallatin, Jackson, and Johnson. On the Forest, this plant was found more recently in Pope County at two natural areas. It was observed most recently at Cretaceous Hills Ecological Area by Paul Marcum in 2010. Mark Basinger observed it at Dean Cemetery East Ecological Area on July 22, 2008. It was also observed at a state natural in Pope County and on private land in Massac County. 58. Guadeloupe Cucumber (Melothria pendula) Guadeloupe cucumber is a climbing herbaceous vine with tendrils that occurs in the southern United States and adjacent Mexico. It reaches its northern range limit in southern Illinois and is often found in damp thickets and gravelly stream beds (Herkert & Ebinger 2002). It has also been found along

xxxiii powerline rights-of-way and trails (Elizabeth Longo, personal observations). In southern Illinois it generally flowers from June to September (Mohlenbrock 2014).

Guadeloupe cucumber was given the Global Heritage Status Rank of G5? in 2000. It is listed as critically imperiled in the District of Columbia, Indiana. Maryland, and West Virginia (NatureServe); imperiled in Illinois (threatened, IESPB) and Kansas; and apparently secure in Georgia, Kentucky, North Carolina, and Virginia. It is listed as not ranked or under review in the remaining states where it has been found (NatureServe 2017).

In Illinois Guadeloupe cucumber has been found in Alexander, Hardin, Jackson, Johnson, Massac, Pope, and Union Counties. On the Forest, it has been found in Dongola Hollow and the Bean Ridge Area in Alexander County; in Hardin County at Panther Den Research Natural Area and at Ramsay Branch; in Jackson County at Fountain Bluff, Cave Valley, and along an access route to a powerline right-of-way; in Pope County at Bell Smith Springs Ecological Area, Russell Cemetery Barrens Ecological Area, near Rock, near Eddyville, and near Waltersburg Road; and at LaRue Pine Hills/Otter Pond Research Natural Area in Union County. Off the Forest, this plant has been found at a state natural area and at several sites on private land in Alexander County; at a couple sites on private land in Hardin County; at several sites at a state natural area and a couple of sites on private land in Johnson County; on private land in Massac County; at a couple of sites on private land in Pope County; at a state natural area in Pulaski County; and at several sites on private land in Union County. 59. Illinois Woodsorrel (Oxalis illinoensis) Illinois woodsorrel is a perennial herb that occurs in rich mesic forests often overlying limestone or other calcareous substrates from southern Illinois (Herkert & Ebinger 2002). It has also been found in southern Indiana, and western Kentucky (NatureServe 2018). In southern Illinois it generally flowers from June to September (Mohlenbrock 2014).

The Nature Conservancy assigned this species a Global Heritage Status Rank of G4Q in 2004. It is listed as critically imperiled in Illinois, imperiled in Indiana, and apparently secure in Kentucky (NatureServe 2018). Schwegman (1982) cites specimens from Tennessee but other sources do not report this species as occurring in Tennessee. Threats to this species include loss of native habitat and droughty conditions.

Illinois woodsorrel has been found in Hardin, Jackson, and Pope Counties in Illinois. Most occurrences are on the Shawnee National Forest, where it has been found in Hardin County at Big Creek Zoological Area and the Kaskaskia Experimental Forest; as well as in Pope County at Copperous Branch Ecological Area, East Fork Oxalis Botanical Area, Lusk Creek Zoological Area, Martha’s Woods Ecological Area, Reddick Hollow Ecological Area, and at One Horse Gap. This species has also been found on private land in Jackson and Hardin Counties. 60. American Ginseng (Panax quinquefolius) American ginseng is a perennial herb of the eastern United States and adjacent Canada (NatureServe 2017). This species has a fleshy rootstock with medicinal value found and is frequently dug up for its roots. In Illinois it blooms during June and July and fruit is typically ripe in mi- August (Fiebig et al. 2001). In Illinois this plant has been found in rich woods and rocky woods (Mohlenbrock 2014).

The Nature Conservancy assigned American ginseng the Global Heritage Rank of G3G4 in 2000. It is ranked as possibly extirpated in the District of Columbia; critically imperiled in Kansas, Louisiana,

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Nebraska, New Jersey, Rhode Island, and South Dakota; imperiled in Connecticut, Delaware, Maryland, Michigan, and New Hampshire, as well as in Ontario and Quebec, Canada; vulnerable in Georgia, Indiana, Iowa, Kentucky, Maine, Massachusetts, Minnesota, Mississippi, New York, North Carolina, Tennessee, Vermont, Virginia, and West Virginia; and apparently secure in Alabama, Arkansas, Missouri, Pennsylvania, South Carolina, and Wisconsin. It is not ranked or under review in Ohio.

The primary threats to American ginseng are commercial overharvest and logging of mesic hardwoods. Even in protected areas such as National Parks and Forests, there is a great deal of poaching due to its valuable root in overseas markets and the difficulty of enforcing existing laws (NatureServe 2017). On the Shawnee National Forest, plants have been over-collected by illegal root-diggers. Population totals rarely exceed one or two dozen young plants. Numerous non-native species threaten the various habitats in which this species occurs (Elizabeth Longo, personal observations).

In Illinois, American ginseng is documented in 84 of 102 counties and is likely present in more (Anderson et al. 1993). It has been reported from all counties on which the Shawnee National Forest has its lands. Natural areas on the Forest where this plant has been found include Ozark Hill Prairie Research Natural Area in Alexander County; Pounds Hollow Ecological Area in Gallatin County; Bulge Hole Ecological Area and Grantsburg Swamp Ecological Area in Johnson County; Burke Branch Research Natural Area, Double Branch Hole Ecological Area, Jackson Hollow Ecological Area, Lusk Creek Canyon Ecological Area, and Lusk Creek Canyon Zoological Area in Pope County; and Atwood Ridge Research Natural Area and LaRue Pine Hills Research Natural Area in Union County (USDA FS 2005). 61. White Wand Beardtongue (Penstemon tubaeflorus) White wand beardtongue is a perennial herb (Nÿboer & Ebinger 2004) that has been found in the central and northeastern United States, as well as eastern Canada (NatureServe 2019). It grows in rich prairies, moist open woods (Nÿboer & Ebinger 2004) and dry woods in Illinois, where it flowers from May to June (Mohlenbrock 2014).

The Nature Conservancy gave white wand beardtongue the Global Heritage Status Rank of G5 in 1993. It is listed as possibly extirpated in Ohio; critically imperiled in Indiana, Iowa, and Tennessee; and apparently secure in Kentucky. It is not ranked, under review, or introduced in the remaining states where it has been found (NatureServe 2019).

White wand beardtongue was listed as an endangered species in Illinois in 2004. Formerly widespread in the state, there are records of this plant in 20 counties. Currently, there are only 10 known element occurrence records from 7 counties. It has become nearly extirpated in Illinois from habitat destruction, collecting, and other development pressures (Edgin & Mankowski 2013). The main threats to this species on the Shawnee National Forest are the destruction of prairies and shading from the encroachment of trees (Elizabeth Longo, personal observations).

Of the 10 counties on which the Shawnee National Forest has its lands, 6 have records of white wand beardtongue—Alexander, Jackson, Johnson, Pope, Saline, and Union. All but the Alexander occurrences are historic (Nÿboer & Ebinger). The most recent record is from a cemetery near Fayville in 2004. The other Alexander County record is from 1992 at the Ozark Hill Prairie Research Natural Area. Keser (1971) found this plant in Saline County at Stoneface in 1969. Mohlenbrock (1985) listed this species in a floristic inventory of LaRue Pine Hills in Union County. Information regarding the Jackson and Pope County occurrences was not available when this report was written.

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62. Wreath Lichen (Phaeophyscia leana) Wreath lichen is found on cottonwood, bald cypress, and other trees in floodplain forests along rivers, oxbow lakes, and backwaters at open, well-lit sites. This lichen grows on trees below the spring high- water marks, where other lichen species are essentially absent. Its range is uncertain, but it has been documented in Illinois, Kentucky, Ohio, Pennsylvania, and Tennessee (NatureServe 2018). In southern Illinois this species occurs on trees in backwater swamps and sloughs (Phillippe 2004c).

The Nature Conservancy ranked this species G2 in 1995 and was last reviewed in 2004. Trends for this species are uncertain due to the relatively recent rediscovery but are thought to be declining due to bank erosion, prolonged flood events and heavy river traffic (NatureServe 2018).

In southern Illinois, wreath lichen has been found on trees adjacent to the Little Wabash and Ohio Rivers in Gallatin, Hardin, Massac, Pope, and White Counties. There are approximately 24 historically known locations in Illinois (Phillippe 2004c). This species occurs at only one site on the Shawnee National Forest, at Tower Rock Recreation Area in Hardin County, a site which is mowed and cleared of brush regularly (Wilhelm & Masters 1994). Elizabeth Shimp and Tony Lear conducted a census of this site in February 2010. 63. Sunbright (Phemeranthus parviflorus) Sunbright is a small perennial herbaceous plant in the Purslane family (succulent plants) growing on exposed sandstone cliffs in Illinois (Mohlenbrock 2014). It is known from Mexico and the central United States where it reaches its eastern extent of its range in southern Illinois (Nÿboer & Ebinger 2004). In Illinois it generally flowers from June to July (Mohlenbrock 2014).

The Nature Conservancy gave sunbright the Global Heritage Status Rank of G5, determined in 1985. It is listed as critically imperiled in Alabama, Iowa, and West Virginia; imperiled in North Dakota; vulnerable in Arizona and Louisiana; and not ranked or under review in Arkansas, Colorado, Kansas, Minnesota, Missouri, Nebraska, New Mexico, Oklahoma, South Dakota, Texas, and Utah (NatureServe 2017). This species was listed as “threatened” (imperiled) by the State of Illinois in 2004. Many of this plant’s populations are located in state parks or federal lands that are commonly used by hikers and horse riders. Trampling has damaged many individuals and has resulted in the extirpation of some populations (Nÿboer & Ebinger). Infestations of Japanese honeysuckle and Nepalese browntop threaten sunbright at several locations on the Shawnee National Forest (Elizabeth Longo, personal observations).

In southern Illinois sunbright is known from Union, Johnson, Massac, and Pope Counties. This plant has been found at several sites on the Forest. In Johnson County it has been found at Bulge Hole (last observed by Kevin Sierzega October 13, 2017), Odum Tract Ecological Areas (last observed by Kevin Sierzega on September 28. 2017), Fink Sandstone Barrens Ecological Area (last seen by Kevin Sierzega on October 2, 2017), near Trigg Tower (by Mark Basinger & A. McCoy on June 16, 1997), and at Schwegman Ecological Area. In Pope County it has been found at Bell Smith Springs (last observed Susanne Masi & Bob Edgin on September 12, 2014), at Hayes Creek-Fox Den Ecological Area (last observed by John White on August 23, 2013), at Jackson Hollow Ecological Area (last observed by Susan Masi on July 18, 2015), and in Lusk Creek Wilderness (last seen by Mark Basinger on July 21, 1992).

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64. Heartleaf Plantain (Plantago cordata) Heartleaf plantain is a perennial aquatic herb that is known from the eastern and central United States and Ontario, Canada. In Illinois it usually occurs in sand or gravel bars of shallow, clear-water streams under a forest canopy (Herkert & Ebinger 2002), where it flowers from April to July (Mohlenbrock 2014). In southern Illinois, this species rarely blooms or gets very tall in stature, most likely the result of excessive shading conditions (USDA FS 2005).

The Nature Conservancy gave this species the Global Heritage Status Rank of G4 in 1994. It has been documented in 20 states and Ontario, Canada, but is presumed extirpated from Kentucky; possibly extirpated from the District of Columbia, Florida, Iowa, Maryland, and Virginia (NatureServe); critically imperiled in Illinois (endangered IESPB), Indiana, Wisconsin, Michigan, Mississippi, Ohio, North Carolina, and Tennessee, as well as Ontario, Canada; imperiled in Alabama and Arkansas; and vulnerable in Georgia, Missouri, and New York. It is under review in South Carolina, but there is no available documentation of occurrences there. This species has declined throughout its range because of stream erosion and siltation from various activities (NatureServe 2017).

Heartleaf plantain has been documented from Jackson, Johnson, Pope, and Saline counties in southern Illinois. On the Forest it has been found at Kinkaid Lake and Cedar Lake in Jackson County; in Johnson County at Simpson Barrens Ecological Area; in Pope County at Copperous Branch and Gyp Williams Hollow Ecological Areas, and near Frieze Cave; and in Saline County at Cave Hill Research Natural Area and north of Flatrock Hollow. It has also been found at state park in Jackson County. 65. Small Green Wood Orchid (Platanthera clavellata) Small green wood orchid is a perennial, tuberous orchid that occurs in the eastern United States and adjacent Canada (Herkert & Ebinger 2002). It is typically found in acidic bogs and wet soil. In southern Illinois it occurs in acidic, forested seeps, usually associated with sphagnum mosses. It generally flowers from June through August (Hill 2007c).

The Nature Conservancy gave small green wood orchid the Global Heritage Status Rank of G5 in 1995. It had been found in 34 states and the District of Columbia, as well as in 6 Canadian provinces. It is ranked as possibly extirpated in North Dakota; critically imperiled in Florida, Illinois (endangered, IESPB), Iowa, and Oklahoma; imperiled in Missouri and Rhode Island; vulnerable in Indiana and Minnesota, as well as in Prince Edward Island, Canada; apparently secure in Kentucky, North Carolina, New Jersey, New York, Ohio, and West Virginia, as well as in New Brunswick, Ontario, and Quebec, Canada; and secure in Delaware, Georgia, and Virginia, as well as in Newfoundland and Nova Scotia, Canada. It not ranked or is unreviewed in the remaining states where it has been found (NatureServe 2018).

Although small green wood orchid is abundant over a broad geographical area, it is declining in some areas (NatureServe), especially at the margins of its range (Hill 2007c). The primary threat to this plant is destruction of its wetland habitat through drainage, channelization, logging, and gravel mining. Other threats are deer browse, cattle grazing, herbicide runoff from agricultural fields and rights-of-way, and invasion of habitats from exotic shrubs (NatureServe). In southern Illinois, threats to small green wood orchid are hydrological changes to seep springs that cause them to dry out or flood, as well as competition from invasive species, such as Nepalese browntop and Japanese honeysuckle (USDA Forest Service 2005).

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Small green wood orchid is found in only a few Illinois counties, most in northeastern Illinois. In the southern part of the state, this orchid has been found only in Pope County. All known occurrences of this orchid in that county are on the Shawnee National Forest, where it has been found at four Forest natural areas—Cretaceous Hills, Dean Cemetery East, Kickasola Cemetery Barrens, and Massac Tower Springs Ecological Areas. 66. Palegreen Orchid (Platanthera flava var. flava) Palegreen orchid is a colonial, perennial orchid with stems that may reach 60 cm in height. It is found in wetlands throughout the southeastern United States but is relatively uncommon. This species can form dense colonies that dominate the communities it occupies. Flowering time for this species is from June through August in most of its range (Taft 2005). It reaches its northwestern range limit in southern Illinois in floodplain forests and swamps (Herkert & Ebinger 2002).

The Nature Conservancy ranked palegreen orchid G4?T4?Q in 1994. It is ranked critically imperiled in Illinois (endangered), Indiana, and New Jersey; imperiled in Missouri, Texas, Alabama, Arkansas, Tennessee, and Nova Scotia, Canada; and vulnerable in Georgia and Virginia. This orchid is apparently secure in Kentucky and Mississippi and is currently not ranked or is under review in Oklahoma, Louisiana, Florida, South Carolina, North Carolina, Maryland, and Michigan (NatureServe 2017). Threats to this species include altered hydrology, conversion of floodplain forest habitat to agricultural land uses, and logging (Taft 2005).

In Illinois palegreen orchid has been found at six counties. There are records of this orchid from Washington and Perry County north of the Shawnee National Forest. On the Forest, it has been found at several sites at Grantsburg Swamp Ecological Area in Johnson County and at one site at Cretaceous Hills Ecological Area in Pope County. Elsewhere in that county, it was discovered at two state nature preserves. Palegreen orchid was recently discovered at a national wildlife refuge in Union County, and there is a historical occurrence on private land from Massac County. 67. Grove Bluegrass (Poa alsodes) Grove bluegrass is a tufted, perennial grass found in the northeastern United States, extending into several Appalachian and Midwestern states, as well as into eastern Canada. Illinois is at the west-central edge of its range, and it has not been found west of the Mississippi River. It generally prefers upland habitat with neutral to slightly acidic soils, growing mainly in shade in cool, mesic hardwood forests (Hill 2007d). In Illinois it grows in mesic forests on wooded bluffs and ravines near Lake Michigan and in rugged wooded areas in the southern part of the state (Herkert & Ebinger 2002). It flowers and bears fruit from May to June in Illinois (Mohlenbrock 2014).

The Nature Conservancy gave grove bluegrass a Global Heritage Status Rank of G4G5 in 1997. It is listed as critically imperiled in Illinois (endangered) and South Carolina, as well as in Prince Edward Island, Canada; imperiled in Indiana; vulnerable in Quebec, Canada; apparently secure in Delaware, Kentucky, Maryland, New Jersey, North Carolina, Virginia, and West Virginia, as well as in Ontario, New Brunswick, and Nova Scotia, Canada; and secure in New York. It is unranked or unreviewed in the remaining 11 states where it has been reported (NatureServe).

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Grove bluegrass is globally secure and not considered under threat; however, it is vulnerable at the margins of its range due to less suitable climate and limited habitat. Threats to this species in Illinois are not known since it is uncertain that it occurs in the state. Potential threats could include fire suppression and canopy closure, as well as extreme clear-cutting. Other possible threats could be loss of habitat, invasive plants, herbivory, and recreational use (Hill 2007d).

Grove bluegrass is easily confused with other Poa species, and there is some question whether it occurs within Illinois. Hill (2007) did not find any voucher specimens from the state when researching his conservation assessment of this grass, and several local experts he consulted told him that some herbarium specimens had been misidentified and were not, in fact, grove bluegrass. However, this species is locally common in Indiana and has been found in three other neighboring states. Descriptions of the habitat at sites where it has been reported in Illinois are consistent with the types of habitat in which it has been found in other states, including adjacent Indiana. It is possible that it occurs in Illinois, but its presence not been adequately confirmed (Hill 2007d).

Grove bluegrass has been reported in widely separated counties in Illinois, although most occurrences are historical. It has been found in Calhoun, Jackson, Lake, Pope, and St. Clair Counties (Hill 2007). In the Shawnee National Forest, it has been reported from Hayes Creek/Fox Den Ecological Area in Pope County and was last seen in 1986 (USDA 2005). It has also been found in a state park in Jackson County and was last observed there in 2008. 68. Procession Flower (Polygala incarnata) Procession flower is an annual herb found in the eastern and central United States and in Ontario, Canada. In Illinois, procession flower is found in, prairies, gravel hills (Mohlenbrock 2014), sand prairies, hill prairies, and barrens (Herkert & Ebinger 2002), where it flowers from July to September (Mohlenbrock 2014).

The Nature Conservancy assigned procession flower the Global Rank of G5 in 1990, likely because of its relatively wide range. It is apparently secure in Kentucky, North Carolina, and Virginia. It is currently unranked or under review by Alabama, Arkansas, Florida, Georgia, Kansas, Louisiana, Mississippi, Missouri, Nebraska, Oklahoma, South Carolina, Tennessee, Texas, and the District of Columbia. It is listed as imperiled in Iowa, Maryland, and Ohio; critically imperiled in Delaware, Illinois, Indiana, Wisconsin, and Ontario, Canada; possibly extirpated in New Jersey and Pennsylvania; and presumed extirpated in Michigan and New York (NatureServe 2018). Threats to this species in Illinois include fire suppression, overgrazing, and habitat destruction from development and mining activities (Herkert & Ebinger 2002).

Procession flower has been found in scattered counties throughout Illinois, but only a few sites are extant. In southern Illinois, this species has verified occurrences only in Pope County, (there is an unverified report from Massac County). All verified occurrences of procession flower are from the Shawnee National Forest, where it has been found at Cretaceous Hills, Dean Cemetery East Barrens, Poco Cemetery Barrens East, and Poco Cemetery Barrens North Ecological Areas, as well as at Old Baldy. 69. Prairie Parsley (Polytaenia nuttallii) Prairie parsley is a perennial herb that is found throughout most of the central United States (NatureServe 2017). It occurs in prairies and rocky woods throughout Illinois (Mohlenbrock 2014) and in

xxxix barrens and glades on the Shawnee and Hoosier National Forests (Heikens 2002). It generally flowers from April to June (Mohlenbrock 2014).

The Nature Conservancy gave this species a Global Heritage Status Rank of G5 in 1984. It is ranked as extirpated in Michigan and Kentucky; possibly extirpated in Minnesota; critically imperiled in Indiana and Tennessee; imperiled in Mississippi and Wisconsin; vulnerable in Iowa and Louisiana; and apparently secure in Nebraska. It is not ranked or currently under review by North Dakota, Illinois, Missouri, Arkansas, Alabama, Kansas, Oklahoma, Texas, and New Mexico (NatureServe 2017).

Although prairie parsley is not listed as rare by the State of Illinois, it has declined across much of the state. At one time, there were over 40 counties in Illinois where this species occurred. However, this species has been extirpated in many of these counties because of habitat destruction and development. On the Shawnee National Forest, the greatest threats to this species are habitat loss, decline in habitat quality, and fire suppression. It is also threatened by several different non-native invasive plants.

In southern Illinois, prairie parsley is historically known from Gallatin, Hardin, Jackson, Johnson, Pope, Saline, and Union Counties. On the Forest, it was first found at Stoneface Research Natural Area by Evers in 1952 in Saline County. It was also found at Simpson Barrens Ecological Area, along a creek in dry-mesic woods in Johnson County, along a Forest road near Williams Hill in a dry oak woodland in Pope County by Mark Basinger in 1992, and by Mohlenbrock at LaRue Pine Hills Research Natural Area in Union County. It has also been reported in Hardin County west of Lamb in 1977 by Evers in 1957, in Jackson County near Elkville in 1948 by Evers Julius R. Swayne, and in Pope County west of Herod by Evers in 1956. 70. Chestnut Oak (Quercus montana) Chestnut oak is a tree that grows to about 100 meters in height. Its range is the eastern United States and adjacent Canada, with southern Illinois at its western margin. It grows on dry, often rocky forests and ridgetops in Illinois (Herkert & Ebinger 2002), where it flowers from April to May (Mohlenbrock 2014).

The Nature Conservancy assigned chestnut oak the Global Rank of G5 in 1984. It is ranked as critically imperiled in Maine; imperiled in Illinois (threatened); apparently secure in Vermont; and secure in Delaware, Indiana, Kentucky, New Jersey, New York, North Carolina, Pennsylvania, Virginia, and West Virginia. It is considered an exotic in Michigan. It is currently not ranked or is under review in Alabama, Connecticut, District of Columbia, Georgia, Louisiana, Maryland, Massachusetts, Mississippi, New Hampshire, Ohio, Rhode Island, South Carolina, and Tennessee (NatureServe 2018).

In Illinois, chestnut oak has been recorded in only a few counties in the extreme southern part of the state and only recently from one county in northern Illinois. In Alexander County, it was found on Forest Service land at Provo Cemetery Barrens and Big Brushy Ridge Ecological Areas, as well as on private land. It was found at High Knob Recreation Area in Gallatin County. In Hardin County it has been found at one site on Forest Service land and another on private land. In Jackson County it was found at a city recreation site. In Saline County this tree was found on Forest Service lands at Reid’s Chapel Ecological Area, Cave Hill Research Natural Area, Dennison Hollow Research Natural Area, and near a trail, as well as on private land. In Union County, chestnut oak has been recorded at Atwood Ridge Research Natural Area.

71. Maryland Meadowbeauty (Rhexia mariana) Maryland meadowbeauty is a rhizomatous perennial herb of the southeastern United States. It reaches its northwestern range limit in southern Missouri and Illinois where it is occasionally found in wet meadows, around ponds, and in seep springs (Nÿboer & Ebinger 2004). It blooms from June to September in Illinois (Mohlenbrock 2014).

The Nature Conservancy assigned this species the Global Heritage Rank of G5 in 1985 (NatureServe). It is listed as endangered in Illinois in Illinois (Nÿboer & Ebinger); critically imperiled in Massachusetts, Pennsylvania, and West Virginia; presumed extirpated in New York; apparently secure in Kentucky; secure in North Carolina and Virginia; and Not Ranked or Under Review in the remaining states where it has been found (NatureServe 2017).

There are reported occurrences of Maryland meadowbeauty in six Illinois counties, five of those in the southern part of the state (Biotics, IDNR, and Mohlenbrock 2011). Most are from Pope County. On the Forest this plant is known from Burke Branch Research Natural Area, Cretaceous Hills Ecological Area, Dean Cemetery West Ecological Area, Dean Cemetery East Ecological Area, and Kickasola Cemetery Barrens Ecological Area in Pope County, as well from a couple of other sites. It was located at a seep spring in Massac County. There is a historical occurrence of this plant in Jackson County at a wet prairie. It was also found on private property in Pope and Saline Counties. In Williamson County, Maryland meadowbeauty has been found at a few sites at a national wildlife refuge, as well as at several sites on private land. 72. Clustered Beaksedge (Rhynchospora glomerata) Clustered beaksedge is a tufted perennial sedge that occurs in the southeastern United States and reaches its northern range limit in southern Illinois (Herkert & Ebinger 2002). In Illinois this sedge grows in moist, sandy soils, where it flowers and produces fruit from July to October (Mohlenbrock 2014).

The Nature Conservancy gave this species a Global Heritage Status Rank of G5 in 1990. Clustered beaksedge is possibly extirpated in the District of Columbia; critically imperiled in Illinois; and imperiled in Delaware. It is listed as vulnerable in Maryland; apparently secure in North Carolina; and secure in Kentucky, Mississippi, and Virginia. It is currently not ranked or is under review in Alabama, Arkansas, Florida, Georgia, Kansas, Louisiana, New Jersey, Oklahoma, South Carolina, Tennessee, and Texas (NatureServe). Threats are to clustered beaksedge include the loss of native habitat from development, invasive species, recreational use, and natural succession (Hill 2006a).

Clustered beaksedge is known from four counties in Illinois. It has been found in two counties in the northeastern part of the state and at Johnson and Pope Counties in the southern part of the state (USDA, NRCS). The southern Illinois sites are on the Shawnee National Forest. Sites in Pope County are at multiple locations in Bell Smith Springs Ecological Area, at a seepage area along a tributary of Copperous Branch, at Lusk Creek Ecological Area, at Lusk Creek Zoological Area, and at Rose Ford. Another site is on Forest Service land near Camp Ondessonk in Johnson County.

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73. Sullivant’s Coneflower (Rudbeckia fulgida var. sullivantii, =R. sullivantii) Sullivant’s coneflower is a composite perennial species of the eastern United States. Across its range it is found in old pastures, prairies, moist open areas, and glades (Molano-Flores 2004). In Illinois it is found in wet woods, wooded swamps, and calcareous fens, where it flowers between July and October (Mohlenbrock 2014).

This plant is not ranked by the Nature Conservancy since it is not recognized as separate from Rudbeckia fulgida var. speciosa. However, it is recognized by the Flora of North America and ITIS (Integrated Taxonomic Information System). Flora of North America lists the following states as having recorded occurrences of Sullivant’s coneflower: Arkansas, Illinois, Indiana, Michigan, Missouri, New York, Ohio, Pennsylvania, and West Virginia. In Illinois it has been reported in twelve counties, most in the eastern part of the state. This plant is not listed as threatened or endangered by the State of Illinois (Molano- Flores 2004).

There are several threats to this plant across its range. The main threat is habitat loss from development, agriculture, grazing, and changes in hydrology. On National Forest lands, it is threatened by recreational use such as trail construction, trampling by hikers, and unauthorized ATV and motorized vehicle use. This plant can sometimes persist in shaded forests but can be threatened by encroachment of successional vegetation. Additional threats include potential gene flow between cultivars and wild types, pathogens, and insect damage (Molano-Flores 2004).

This plant has been found on the Shawnee National Forest at only a few sites in Pope County. It is known from a seep spring at Kickasola Cemetery Barrens Ecological Area and near an acid seep at Poco Barrens in the Cretaceous Hills (Molano-Flores 2004). Rudbeckia fulgida has also been found in Belle Smith Springs (mesic upland forest) although it is unclear as to whether this is the variety sullivantii. 74. Longbeak Arrowhead (Sagittaria australis) Longbeak arrowhead (formerly listed as S. longirostra in Illinois) is a stoloniferous emergent, perennial herb that is found in the eastern United States where it reaches its northwestern range limit in southern Illinois (Herkert & Ebinger 2002). In Illinois it has been found in springy woods, where it blooms from July to September (Mohlenbrock 2014).

The Nature Conservancy gave this species a Global Heritage Status Rank of G5 in 1988. It is listed as critically imperiled in New Jersey, and Washington DC; imperiled in Indiana; apparently secure in Delaware, Kentucky, Ohio, and Virginia; secure in West Virginia; and unranked or under review in the remaining states where it is found (NatureServe 2018). In Illinois it is listed as endangered (Herkert & Ebinger 2002). Threats to this species in southern Illinois include changes in hydrology, woody encroachment, and non-native invasive species, such as Nepalese browntop (Basinger 2009).

There is some discrepancy among various sources regarding the distribution of this longbeak arrowhead in Illinois. According to Herkert and Ebinger (2002), there are historical records of it in three southern Illinois counties—Pope, Pulaski, and Union. Mohlenbrock (2011) stated that this plant has been found in a few northwestern counties and in Alexander, Pope, and Union Counties in extreme southern Illinois. Collection records at the Illinois Nature History Survey Herbarium contain a 1947 specimen of this plant found in Carrol County, which is in northwest Illinois. On the Shawnee National Forest, longbeak

xlii arrowhead was found at Cretaceous Hills Ecological Area in Pope County and at LaRue Pine Hills/Otter Pond Research Natural Area in Union County. 75. Small’s Blacksnakeroot (Sanicula smallii) Small’s blacksnakeroot is a perennial herb with thickened roots that is found in the southeastern United States, reaching its northwestern range limit in southern Illinois. In Illinois it is found in dry to mesic upland woods (Nÿboer & Ebinger 2004) and rich wood (Mohlenbrock 2014). It blooms from May to June in Missouri (Yatskievych 2006).

The Nature Conservancy gave this species a Global Heritage Status Rank of G5 in 1986. It is listed as possibly extirpated in Missouri; critically imperiled (endangered) in Illinois; imperiled in Indiana; vulnerable in Arkansas and West Virginia; apparently secure in Virginian; and secure in Kentucky and North Carolina. It is not ranked or is under review in the remaining states where in has been found (NatureServe 2019).

Small’s blacksnakeroot has been found at only one site in Illinois. That location is on Forest Service and private land in Hardin County. A trail runs through part of this population, serving as a conduit for non- native invasive plants. Several infestations threaten this population. 76. Early Saxifrage (Saxifraga virginiensis, =Micranthes virginiensis) Early saxifrage is a perennial herb with a flowering scape that reaches 10 to 40 cm in height. It ranges from eastern Canada, south into the eastern United States. It is restricted to sandstone canyons and mesic rocky ravine forests in extreme southern Illinois (Herkert & Ebinger 2002), where it flowers from April to June (Mohlenbrock 2014).

The Nature Conservancy gave this species a Global Heritage Status Rank of G5 in 1983. It is listed as possibly extirpated in Louisiana; critically imperiled in Illinois (endangered) and New Brunswick, Canada; imperiled in Rhode Island; vulnerable in Arkansas, Delaware, Indiana, and Manitoba, Canada; apparently secure in Mississippi and Quebec, Canada; and secure in Kentucky, New York, North Carolina, Virginia, West Virginia, and Ontario, Canada. It is not ranked or is under review in the remaining states where in has been found (NatureServe 2019). In southern Illinois, the greatest threats to this species is habitat destruction, excessive recreational use on rock ledges, (USDA Forest Service 2005), and competition from Japanese honeysuckle and autumn olive (Elizabeth Longo, personal observations).

In Illinois early saxifrage has been found in a few northern counties and at Hardin County in southern Illinois. On the Shawnee National Forest, this plant has been found at Cane Creek Botanical Area, Panther Hollow Research Natural Area, a site near Elizabethtown, Buckhart Ravine, Battery Rock, South of Sturgeon Hill, and at Crow Hill. It has also been found at a couple of sites on private land. 77. Leafy Bulrush (Scirpus polyphyllus) Leafy bulrush is a rhizomatous, perennial sedge with culms reaching 0.5 to 1.5 meters in height. It has been found in the eastern United States, reaching its western range limit in Illinois. It is found in open forested seeps (Herkert & Ebinger 2002), where it blooms from July to September (Mohlenbrock 2014).

The Nature Conservancy gave this species a Global Heritage Status Rank of G5 in 1986 (NatureServe). It is listed as possibly extirpated in New Hampshire; imperiled in Arkansas, Massachusetts, , and Illinois; vulnerable in Missouri and Vermont; apparently secure in Delaware, Kentucky, New Jersey, and North

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Carolina; and secure in New York, Virginia, and West Virginia. It is listed as unranked or under review in the remaining states where it is found (NatureServe 2018).

Leafy bulrush has been found in several widely scattered counites throughout Illinois. In southern Illinois, it has been reported from Hardin, Massac, and Pope Counties. It was found on private land in Massac County, as well as on Forest Service land. In the other two counties this species has been found in seep springs, primarily at natural areas within the Shawnee National Forest. In Hardin County it was found at Panther Hollow Research Natural Area. In Pope County this sedge has been found at Belle Smith Springs Ecological Area, Cretaceous Hills Ecological Area, Dean Cemetery West Ecological Area, Kickasola Springs Ecological Area, Massac Tower Springs Ecological Area, at another Forest Service site, and on private land. 78. Littlehead Nutrush (Scleria oligantha) Littlehead nutrush is a perennial sedge that grows at mostly shady sites in mesic to xeric woodlands, glades, and wet meadows. It is found in the southeastern and south central United States, reaching its northern range limit in southern Illinois. It is also found in Mexico and Central America (FNA 2003). It blooms from June to September in Illinois (Mohlenbrock 2014).

NatureServe listed littlehead nutrush as a G5 in 1984. It is ranked critically imperiled in West Virginia; imperiled in Ohio; vulnerable in Illinois and Indiana; apparently secure in Kentucky, Virginia, and North Carolina; and secure in Mississippi. It is listed as an exotic in New Jersey. It is not ranked or under review in Maryland, District of Columbia, South Carolina, Georgia, Florida, Alabama, Tennessee, Missouri, Arkansas, Louisiana, Oklahoma, and Texas (NatureServe 2017).

Littlehead nutrush is known from a single location in Illinois. It was found on the Shawnee National Forest at Barker Bluff Research Natural Area in Hardin County. This species was collected by Mark Basinger and Jody Shimp on July 8, 1998 at the edge of a limestone glade opening, which is now closed in by eastern red cedar. Plants growing at the site are typical of barrens and prairies (Tucker & Ebinger 2011). 79. Fewflower Nutrush (Scleria pauciflora) Fewflower nutrush is a perennial, rhizomatous sedge found in the eastern United States and adjacent Mexico. In Illinois it has been reported from open, sandy woods, as well as from barrens, glades, and disturbed fields (Nÿboer & Ebinger 2004), where it flowers from June to August (Mohlenbrock 2014).

The Nature Conservancy assigned fewflower nutrush the global rank of G5 in 2002. It is ranked critically imperiled in Delaware, Illinois, Massachusetts, Michigan, Rhode Island, Texas, West Virginia, and Ontario, Canada; imperiled in Maryland, Ohio, and Pennsylvania; vulnerable in Arkansas and Indiana; apparently secure in Mississippi and North Carolina; and secure in North Carolina (NatureServe 2017). In Illinois it is ranked as endangered, critically imperiled (IESPB 2015). This sedge is not ranked or under review in the remaining states where it has been found (NatureServe). Overall threats include its vulnerability to forest succession and development (USDA FS 2012).

Fewflower nutrush has been found in a few counties in Illinois. Three are in northern Illinois and the rest in the southern Illinois at Hardin, Jackson, Johnson, Pope, Massac, Randolph, Union, and Williamson Counties. On the Shawnee National Forest, this sedge has been identified at Keeling Hill South Ecological Area in Hardin County; at three sites near Kinkaid Lake in Jackson County; at Fink Sandstone

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Barrens Ecological Area in Johnson County; and at Cretaceous Hills, Dean Cemetery East, Dean Cemetery West, Snow Springs, Kickasola Cemetery Barrens Ecological Areas, a recreation area, and another Forest site in Pope County. It has been found on private land in Massac County, a state nature preserve in Pope County, a privately owned nature preserve in Randolph County, and a national wildlife refuge in Williamson County. Information regarding the Union County occurrence was unavailable when this report was written. 80. Blue Ridge Catchfly (Silene ovata) Blue ridge catchfly is a multi-stemmed perennial found in the southeastern United States, reaching its northern range limit in extreme southern Illinois (Herkert & Ebinger 2002). In Illinois, it is found in rich woods where it blooms in August (Mohlenbrock 2014).

The Nature Conservancy assigned Blue Ridge catchfly the global rank of G3 in 2004. This species is known from 11 states and is listed as critically imperiled in Illinois, Indiana, Kentucky, Virginia, Mississippi, and Georgia; imperiled in Tennessee and Alabama; and vulnerable in Arkansas and North Carolina. It is presumed extirpated in South Carolina (NatureServe 2019).

Threats to Blue Ridge catchfly include logging, clear-cutting, land-use conversion, and habitat fragmentation. It is not an aggressive species, and competition from exotic species can be a threat to the few populations in Illinois (Hill 2003c). Increased recreational use in the vicinity of populations of southern Illinois causes the greatest threat, especially at Sturgeon Hill. User-created equestrian trails go through populations causing trampling, browsing, destruction of rootstalk, and removal of the thin-soil layers (Basinger 1998).

Blue Ridge catchfly has been found only at Hardin County in Illinois. It was first found in Illinois by Jody Shimp in 1994, who located 5 populations. Elizabeth Shimp discovered another population in 1999. All but two sites are on the Forest. Two Forest sites are on protected land—at Barker Bluff Research Natural Area and Panther Hollow Research Natural Area. The unprotected sites are at Sturgeon Hill and Cane Creek. Two areas occur on private property (one population occurs both on unprotected Forest Service land and on adjacent private property, with one of the sites now owned by The Nature Conservancy. 81. Whorled Rosinweed (Silphium trifoliatum) Whorled rosinweed is a perennial herb, with stems 1-2 meters tall. It is found in the southeastern United States, where it reaches its northwestern range limit in southern Illinois. Across its range, this plant grows in prairies, glades, barrens and savannas (Herkert & Ebinger). In Illinois is found it rocky woods, where it blooms from July to September (Mohlenbrock 2014).

The Nature Conservancy assigned whorled rosinweed the global rank of G4? Om 1994. This species is ranked as critically imperiled in the Washington DC; vulnerable in Maryland and Tennessee; apparently secure in Mississippi, Virginia, and West Virginia; and secure in Kentucky. It is not ranked or under review in Alabama, Georgia, Indiana, Louisiana, Michigan, New York, North Carolina, Ohio, Pennsylvania, and South Carolina (NatureServe 2019). It is listed as endangered in Illinois (Herkert & Ebinger 2002). Threats to this species include fire suppression and succession of woody vegetation into open habitats, conversion of remnant prairies and barrens for development, herbicide use on roadsides, invasion by exotic plant species, and quarries for limestone (USDA FS 2005).

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Whorled rosinweed has only been found in Hardin County in Illinois. Two occurrences have been found, both on the Shawnee National Forest. It was first discovered by Steve Olson and Max Hutchinson at Barker Bluff Research Natural Area in 1986. It was later found at Whoopie Cat Mountain Ecological Area by Lawrence Stritch and Jody Shimp in 1992. 82. Spring Lady’s Tresses (Spiranthes vernalis) Spring lady’s tresses is a perennial tuberous orchid reaching 60 cm in height. Its range is the southeastern and south-central United States, north into southern New England. It occurs in acidic soils in prairies, rich woodland barrens and old native fields in the southern third of Illinois (Herkert & Ebinger 2002), where it blooms from July to August (Mohlenbrock 2014).

The Nature Conservancy assigned spring lady’s tresses the rank of G5 in 1984. It is ranked as critically imperiled in New York, Pennsylvania, Illinois and Iowa; imperiled in Indiana, South Dakota, Nebraska, Massachusetts, Rhode Island, and Delaware; vulnerable in West Virginia, New Jersey and North Carolina; apparently secure in Georgia; and secure in Virginia and Kentucky. It is not ranked or is under review in Wisconsin, Michigan, Connecticut, Maryland, the District of Columbia, Ohio, South Carolina, Florida, Tennessee, Alabama, Mississippi, Louisiana, Arkansas, Missouri, Kansas, Oklahoma, Texas, and New Mexico (NatureServe 2017).

In Illinois, spring lady’s tresses has been found in several counties north of Shawnee National Forest lands, as well as in Jackson, Johnson, Pope, Saline, Union, and Williamson Counties. In Jackson County, this orchid was discovered on private land and at Oakwood Bottoms. In Johnson County, it was found at two sites on private land. In Pope County, this species has been located at on the Forest at Burke Branch Research Natural Area, Cretaceous Hills Ecological Area, Dean East Cemetery Barrens Ecological Area, near Snow Springs Natural Area, and at Lusk Creek Wilderness. It has also been found at a state natural area and at two sites on private land in that county. This orchid was also found on private land in Saline County and at a national wildlife refuge in Williamson County. No information was available regarding the Union County occurrence at the time this report was written. 83. Star Chickweed (Stellaria pubera) Star chickweed is a perennial herb that grows to be 15-40 cm long. It is found in the southeastern United States, where it reaches its northern range limit in Illinois. In Illinois it occurs on bluffs and in rocky woods (Herkert & Ebinger 2002), while it is found in rich woods and alluvial bottomlands across its range (FNA 2005). It blooms from March to May in Illinois (Mohlenbrock 2014).

The Nature Conservancy assigned star chickweed the rank of G5 in 1991. It is ranked as possibly extirpated in New Jersey; critically imperiled (endangered) in Illinois; imperiled in Mississippi; and secure in the District of Columbia, Kentucky, North Carolina, Virginia, and West Virginia. It is not ranked or is under review in Alabama, Florida, Georgia, Indiana, Louisiana, Maryland, Ohio, Pennsylvania, and South Carolina. It is considered exotic in Delaware and New York (NatureServe 2018).

In Illinois, star chickweed has been found in Cook, Hardin, Pope (Herkert & Ebinger 2002), DuPage, and Will (Mohlenbrock 2014) Counties in Illinois, but the Cook County occurrence is believed to be an introduction (Herkert & Ebinger 2002). The southern Illinois sites were found on the Shawnee National Forest. In Hardin County, this species was located at Cane Creek in Hardin County. It has also been found in Pope County at Burke Branch Research Natural Area, near Bay Creek, and at Cooney Creek.

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Forest Service sites are threatened by infestations of the invasive, non-native grass, Nepalese browntop (Elizabeth Longo, personal observations). 84. Eastern Featherbells (Stenanthium gramineum) Eastern featherbells is a bulbous perennial herb found in the eastern United States, with Illinois at the northwestern margin of its range (Herkert & Ebinger 2002). It is scattered in the southern half of Illinois where it occurs in mesic floodplain forests and upland forests (Edgin 2002). Although this herb can persist under shade, it benefits from canopy gap openings and increased light (Phillipe 2005d). In Illinois, this plant flowers from June to August (Mohlenbrock 2014).

The Nature Conservancy assigned this species the rank of G4G5 in 1995. It is ranked critically imperiled in Illinois (endangered), Indiana, Oklahoma, Mississippi, Pennsylvania, and Maryland; imperiled in Ohio and Kentucky; and vulnerable in North Carolina, West Virginia, Arkansas and Louisiana. It is apparently secure in Virginia but is extirpated from the District of Columbia. It is currently not ranked or under review in Texas, Alabama, Georgia, Florida, South Carolina, Tennessee, and Missouri. Michigan lists it as an exotic (NatureServe). Primary threats in Illinois include creek bank erosion, road construction, and trampling from equestrian use (Edgin 2002). Competition from invasive plants is also a threat, as is grazing, logging, woody encroachment, and the absence of fire (Phillipe 2004d).

Eastern featherbells is historically known from 13 counties in Illinois but is extant in only seven (Phillippe 2004d). In southern Illinois it has been found in Gallatin, Jackson, Johnson, Massac, Pope, Pulaski, and Union Counties. On the Forest it has been found at in a gravel wash at an intermittent steam (horse trail going through colony) in Gallatin County; Kinkaid Lake (Chris Benda 9/10/2019); Grantsburg Swamp in Johnson County (Mark Basinger and Elizabeth Longo Shimp on May 2, 1994); near Bay Creek at Bell Smith Springs (Bob Edgin on July 21, 2002), near Copperous Branch (Bob Edgin July 19, 2002), Big Grand Pierre Creek (John Taft 9/12/1989), in a mesic forest at Burke Branch Research Natural Area (John Schwegman on June 10, 1987), and northwest of Golconda (Chris Benda October 15, 2018) in Pope County. Southern Illinois sites of this plant not on the Forest include: the edge of a pond in Jackson County (not relocated in 2002), a gravel wash at Ferne Clyffe State Park (not relocated in 2002), Mermet Lake in Massac County (not relocated in 2002 and feared extirpated), and in a floodplain forest in Pulaski County. The Union County record is unverified, and the location uncertain at the time this report was written. 85. American Snowbell (Styrax americanus) American snowbell is a shrub growing up to 3 meters tall. Its range is the southeastern United States. In Illinois is occurs in southern floodplain forests and swamps (Herkert & Ebinger 2002), where it blooms from April to May (Mohlenbrock 2014).

The Nature Conservancy assigned American snowbell the rank of G5 in 1985. It is listed as critically imperiled in Oklahoma; imperiled in Illinois; vulnerable in Indiana, Kentucky, North Carolina, and Virginia; and not ranked or under review in Alabama, Arkansas, District of Columbia, Florida, Georgia, Louisiana, Missouri, Mississippi, New Jersey, Tennessee, South Carolina, and Texas (NatureServe 2017).

American snowbell has been found in scattered counties in central and southern Illinois. Southern Illinois counties where it has been found are Alexander, Gallatin, Jackson, Johnson, Massac, Pope, and

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Pulaski. It has been found at only one site on the Shawnee National Forest at Grantsburg Swamp Ecological Area. Other southern Illinois locations of this plant are on state and private lands: a state conservation area and a roadside swamp in Alexander County; Heron Pond, Cache River State Natural Area, north of Reevesville, and near East Vienna in Johnson County; a state nature preserve, a state conservation area, and a couple sites on private land in Massac County; a state nature preserve in Pope County; a state nature preserve and state natural area in Pulaski County; and in swampy woods on private land in Union County. No information was available for the Jackson County occurrence when this report was written. 86. Bigleaf Snowbell (Styrax grandifolius) Bigleaf snowbell is a colonial shrub or small tree. Its range is the southeastern and south central United States, where it grows in dry to mesic upland forest, generally flowering from April to May (Hill 2007a). In Illinois, this plant blooms in May (Mohlenbrock 2014).

Bigleaf snowbell was given the global rank of G5 in 1985 by the Nature Conservancy. It is listed as vulnerable in Virginia; critically imperiled in Kentucky, Illinois and Indiana; and presumed extirpated in Ohio. It is ranked as apparently secure in North Carolina and is not ranked or under review in Texas, Arkansas, Louisiana, Mississippi, Alabama, Tennessee, Georgia, South Carolina, and Florida (NatureServe 2019). Threats to this species include lack of genetic variability at the edge of the species range, habitat fragmentation, drought and freezing, land development, logging, deer browsing, and competing woody encroachment (Hill 2007a).

Bigleaf snowbell was known in Illinois only from Alexander County until recently, when a second site was found in Pope County. Both sites are located on the Shawnee National Forest. It was discovered by John Schwegman on May 21, 1968 in a rocky, mesic upland woods at Wolf Creek Botanical Area and was last seen there on May 11, 2018 by Chris Benda. An additional site was found by Chris Evans in Burden Falls Wilderness in Pope County on December 4, 2018. The Wolf Creek site is heavily shaded, flowering rarely occurs, and its reproduction is asexual (Schwegman 1992). This location is also threatened by multiflora rose and Japanese honeysuckle (Hill 2007a). 87. Guyandotte Beauty (Synandra hispidula) Guyandotte beauty is a perennial herb in the mint family. It is found in the southeastern United States, with Illinois at its northwestern range limit (Herkert & Ebinger 2002). It grows in shaded rich, wet to moist mesic upland forests on slopes in cool, moist places, usually in at the bases of deep, wooded ravines in deep leaf mold. It usually is found on calcareous substrates (Hill 2007e). On the Shawnee National Forest, its roots are found growing just below detritus of thick leaf litter, often adjacent to fire dependent communities (USDA FS 2005). In Illinois it blooms and bears fruit from May to June (Mohlenbrock 2014).

Guyandotte beauty was given the global rank of G4 in 1988 by the Nature Conservancy. It is listed as critically imperiled in Alabama, Illinois (endangered), North Carolina, and West Virginia; imperiled in Tennessee and Virginia; vulnerable in Indiana; and apparently secure in Kentucky. It is not ranked or under review in Connecticut, New Jersey, and Ohio (NatureServe 2019). It is most common in Indiana, Kentucky, Ohio and Tennessee, but may no longer be extant in New Jersey and is known only from historic records in North Carolina (Hill 2007e). Range-wide,

xlviii threats to Guyandotte beauty include land-use conversion, habitat fragmentation, and forest management practices (NatureServe 2019).

In Illinois, Guyandotte beauty has been found in Jackson and Union Counties in Illinois. On the Shawnee National Forest, it has been found in Jackson County at the Silvey Pond Botanical Area vicinity at several sites, in the Cedar Creek/Bear Creek vicinity west of Cedar Lake at several sites, and in Cave Valley. Nepalese browntop infestations threaten populations of Guyandotte beauty at the Cedar Creek/Cave Valley. It has also been found at a state park and on private land in Jackson County and on private land in Williamson County. 88. New York Fern (Thelypteris noveboracensis) New York Fern is a perennial, deciduous fern that grows in colonies from branching rhizomes. Its range is the eastern United States and Canada. It grows on acidic substrates in mixed conifer-hardwood forests, seep springs, swamp margins, sandstone cliffs, and roadsides (Hill 2006b). Spores are formed from June through September (Mohlenbrock 2014).

New York fern was assigned the global rank of G5 in 1984 by The Nature Conservancy. It is listed as vulnerable in Arkansas and critically imperiled in Louisiana and Illinois. It is ranked as apparently secure in and Newfoundland, Ontario, and Quebec, Canada; and secure in Kentucky, New York, North Carolina, Virginia, and West Virginia, as well as in New Brunswick, Nova Scotia, and Prince Edward Island, Canada. It is currently not ranked or under review in Alabama, Georgia, Indiana, Maine, Maryland, Massachusetts, Michigan, Mississippi, New Hampshire, Ohio, Oklahoma, Pennsylvania, Rhode Island, South Carolina, Tennessee, and Vermont (NatureServe 2019).

Although New York fern is secure, it is threatened at the margin of its range in the Midwest and southern United States. Threats include trampling from hikers and equestrians, soil compaction, runoff from pollutants and herbicides, clear cutting, and exotic plants such as Japanese and bush honeysuckle. In Illinois the major threat to this fern is natural succession of seep springs by woody species that shades out herbaceous plants (Hill 2006b).

New York fern was historically known from 6 scattered counties in Illinois in fens and moist sandy areas but is now only known from a single location in southern Illinois within Pope County. This species was documented near a damp sandy seep spring in the woods at Cretaceous Hills Ecological Area (mesic upland forest) on June 27, 1967 by John Schwegman (collection #82). It was last observed on May 30, 2007 by Schwegman, Martha Schwegman, and Elizabeth Longo Shimp. 89. Pale False Mannagrass (Torreyochloa pallida) Pale false mannagrass is a perennial, semi-aquatic grass that grows up to 1 meter tall (Herkert & Ebinger 2002). It is widespread in the United States and Canada except for the central states (NatureServe). In Illinois, this grass occurs in shallow, standing water in swamps and marshes (Herkert & Ebinger 2002), where it blooms from May to August (Mohlenbrock 2014).

New York fern was assigned the global rank of G5 in 2005 by The Nature Conservancy. It is listed as possibly extirpated in Georgia and Kentucky; critically imperiled in Illinois, North Carolina, South Carolina, Tennessee, and British Columbia, Canada; imperiled in West Virginia, and Manitoba and Saskatchewan, Canada; vulnerable in Maryland, Minnesota, and Wyoming; apparently secure in Virginia, and Nova Scotia, Ontario, and Prince Edward Island, Canada; and secure in New Brunswick, Canada. It is

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unranked or under review in the remaining states and provinces where it has been found. This grass is threatened by degradation of its wetland habitat from land conversion, habitat fragmentation, sedimentation, and to a lesser extent by forest management practices (NatureServe 2019).

In Illinois pale false mannagrass has been documented from Montgomery County in northern Illinois and from Jackson and Union Counties in southern Illinois (Mohlenbrock 2014). Both southern Illinois occurrences are on Forest Service land, one at LaRue-Pine Hills/Otter Pond Research Natural Area in Union County (found by Ron Henry (#1220) on May 15, 1966, then redocumented by Rick Phillippe May 26, 1988) and the other at Oakwood Bottoms (found by Rick Phillippe on May 25, 1993) in Jackson County. 90. Heartleaf Noseburn (Tragia cordata) Heartleaf noseburn is a perennial vine found in the southeastern United States (USDA, NRCS). In Illinois it is found in dry woods and bluff, where it flowers from July to September (Mohlenbrock 2014).

Heartleaf noseburn was assigned the global rank of by G4 by The Nature Conservancy in 1984. It is listed as imperiled in Georgia, Indiana, and Missouri and vulnerable in Kentucky. This species is not ranked or is currently under review in Alabama, Arkansas, Florida, Illinois, Louisiana, Mississippi, Oklahoma, Tennessee, and Texas (NatureServe 2018).

Heartleaf noseburn has been found in Gallatin, Hardin, Johnson, and Pope Counties in Illinois. On the Forest it has been found at three locations. Mark Basinger and Dave Ketzner collected this species (#7564) on 27 September 1993 in the floodplain woods along an intermittent creek in Pope County. Eric Ulaszek (#2277) also collected it in Pope County on 27 September 1994 at the Dog Creek Barrens Ecological Area in a barrens restoration area. Basinger and Ketzner (#6620) also collected it in Gallatin County on 30 August 1993 along a trail, which was running along an intermittent stream. It has become increasingly scarce in the past couple of decades (Elizabeth Longo, personal observations). 91. Appalachian Bristle Fern (Trichomanes boschianum) Appalachian bristle fern is a perennial fern occurring in the southeastern United States. This species occurs in moist, humid crevices of sandstone overhangs and rockhouses where temperature and moisture are typically constant year round (Hill 2003a). In Illinois it is found beneath moist, overhanging sandstone cliffs or occasionally on sandstone entrances to caves (Herkert & Ebinger 2002), where it is fertile from June to September (Mohlenbrock 2014).

NatureServe lists Appalachian bristle fern with a Global Ranking of G4 (last reviewed 1n 1986). It is ranked as critically imperiled in Georgia (NatureServe), Illinois, Indiana, Mississippi, North Carolina, Ohio, South Carolina, Tennessee, Virginia, and West Virginia; imperiled in Arkansas; and vulnerable in Alabama. The primary threat to this species is its limited distribution (NatureServe 2017). Plants are also very sensitive to drought and have been damaged by over- collection, recreational activities including camping, illegal artifact hunting and rock climbing. Trends for Appalachian bristle fern are thought to be declining throughout much of its range (Hill 200a).

Populations in Illinois have been documented from sites in Gallatin (3), Hardin (1), Johnson (7), Pope (5) and Union (1) counties (Hill 2003a). It was relocated at 16 of its 23 original locations

and additionally found at 2 new sites near former locations (Schwegman 1999). Areas that were relocated on Forest lands were Belle Smith Springs (north-facing sandstone shelter), Sand Cave, Double Branch Hole (north-facing sandstone cliff), Jackson Hollow Ecological Areas (first discovered by Mary Steagall on August 2, 1932, collection #37), and Jackson Falls Recreation Area in Pope County; Bulge Hole Ecological Area in Johnson County; and Brown’s Hole Zoological Area in Harding County. Seven of the former locations are sites where the populations are feared extirpated, including sites on the Forest at Pounds, Hollow, High Knob, and Thacker Hollow in Gallatin County, and at Panther Den Wilderness in Union County. 92. Buffalo Clover (Trifolium reflexum) Buffalo clover is an annual or biennial clover that is found in the eastern and central United States and Canada. It is typically found in open upland forests and prairies (Taft 2004b). In Illinois it has been found in dry to mesic savannas, upland forests, prairies, and flatwoods (Herkert & Ebinger 2002). This species generally flowers and bears fruit from May through July, rapidly senescing afterwards (Taft 2005).

Buffalo clover was assigned the global rank of by G3G4The Nature Conservancy in 2004. It is listed as presumed extirpated in the District of Columbia, New Jersey, Pennsylvania, and Ontario, Canada; possibly extirpated in Maryland; critically imperiled in Illinois, Kentucky, Nebraska, North Carolina, Ohio, Tennessee, Virginia, and West Virginia; imperiled in Kansas; and vulnerable in Missouri. This species is not ranked or is currently under review in Alabama, Arkansas, Florida, Georgia, Indiana, Louisiana, Mississippi, Oklahoma, South Carolina, and Texas. Iowa lists it as an exotic (NatureServe 2017). Threats to buffalo clover include fire suppression at open woodlands and prairies, habitat destruction from agriculture and development, and non-native species’ invasion. The decline of native clovers in general may be attributed to habitat destruction, poor dispersal to new habitat, loss of a natural grazing regime from buffalo, competition from exotic plant species, and reduced fire frequency (Taft 2004b).

Buffalo clover was once scattered throughout Illinois in dry-mesic savannas, upland forests, prairies, and flatwoods. It is now nearly extirpated in the state and occurs in less than half of the counties that it did historically (Taft 2004b). In southern Illinois it is known from extant populations in Jackson and Johnson counties. There is an unconfirmed report of this species from Gallatin County. It is known from a rocky, dry-mesic upland forest adjacent to limestone barrens at Simpson Township Barrens Ecological Area in Johnson County (collection by Elizabeth Longo Shimp, June 12, 1996) and at Little Grand Canyon/Horseshoe Bluff Ecological Area (discovered by David King and collected by Jody Shimp in June 6, 1994, collection #5290) in Jackson County. 93. Green Trillium (Trillium viride) Green trillium is a perennial rhizomatous herb with stems reaching up to 45 cm tall. Its range is southwestern Illinois and east-central Missouri. In Illinois, It is restricted to the extreme western and southern counties, where it has been found in varied habitats: forested bottomlands, talus slopes, blufftops, and prairies (Herkert & Ebinger 2002). It generally blooms from April to May (Mohlenbrock 2014).

Wood wakerobin was given the Global Heritage Status Rank of G4G5 in 1984 (NatureServe 2019). This species is listed as endangered in Illinois (IESPB 2015) and presumed extirpated in Michigan. It is listed as not ranked or under review in Missouri and the District of Columbia (NatureServe 2019).

In Illinois, wood wakerobin is restricted to the extreme western and southern counties (Herkert & Ebinger 2002). In southern Illinois, it has been found in Franklin, Johnson, Union, and Williamson Counties. It has been observed most recently at a state park in Union County. There is also a historical occurrence of this species on the Shawnee National Forest at LaRue Pine Hills/Otter Pond Research Natural Area in Union County. In Williamson County, there is a historical occurrence of this plant on private land. The Franklin County occurrence was last observed in 1982. 94. Threebirds (Triphora trianthophora) Threebirds is a perennial orchid that is widespread but relatively uncommon throughout its range. It is found in the eastern United States, Central America, and Ontario, Canada. It grows in a variety of habitats over its range—from bogs, swamps and floodplain forests to slopes in cove forests. It is most often found in mesic to wet deciduous forests with filtered light and humus rich soils (Ramstetter). In Illinois this orchid has been found in rich woods, where it flowers and bears fruit from August to October (Mohlenbrock 2014).

The Nature Conservancy assigned threebirds the Global Rank of G4? in 2018. It is listed as possibly extirpated in the District of Columbia; critically imperiled in Connecticut, Delaware, Kansas, Maryland, Massachusetts, Michigan, New Jersey, Pennsylvania, Vermont, Virginia, and Ontario, Canada; imperiled in Georgia, Louisiana, Maine, Mississippi, New Hampshire, New York, North Carolina, Ohio, Oklahoma, South Carolina, West Virginia, and Wisconsin; vulnerable in Florida, Illinois, and Iowa; and unranked or unreviewed in the remaining states where it is found (NatureServe 2018). Threats to this orchid include herbivory (Ramstetter), land use conversion, logging, habitat fragmentation and degradation, drying out of humus on the forest floor after logging, trampling and over collecting (NatureServe 2018).

Threebirds is found in scattered counties across Illinois. In southern Illinois, it has been found in Alexander, Jackson, Johnson, Randolph, Saline, and Union Counties. In Jackson County this plant has been found on the Shawnee National Forest at a couple of sites--at Hickory Ridge by Julius Swayne in 1951 and by David Ketzner in the mid-1980’s near Kinkaid Lake. This orchid was subsequently relocated in the Kinkaid Lake area by Shannan Sharp in 2016 and by Chris Benda in 2018 and 2019. This species was also found on the Forest in Saline County just west of the P & E Land and Water Reserve. Off the Forest, it has was identified at state nature preserves in Alexander, Johnson, and Randolph Counties. In Union County it was found on private land, as well as at a state Forest. 95. Deerberry (Vaccinium stamineum) Deerberry is a deciduous shrub occurring in the eastern United States and adjacent Canada (Nÿboer & Ebinger 2004). It is found in dry open rocky forests, thickets, and clearings in acidic, often nutrient poor soils. It spreads vegetatively through rhizomes making it hard to determine how many individuals are actually in a population (Hill 2002a). This shrub flowers from May to June (Mohlenbrock 2014).

The Nature Conservancy assigned deerberry the Global Heritage Status Rank of G5 in 1984. It is ranked critically imperiled in Kansas, Vermont, and Ontario, Canada. It is ranked secure in New Jersey, Delaware, Virginia, North Carolina, West Virginia, Kentucky, and Missouri; it is currently not ranked or under review in Maine, Massachusetts, Rhode Island, Connecticut, Maryland, the District of Columbia, Pennsylvania, Ohio, Indiana, South Carolina, Georgia, Tennessee, Alabama, Florida, Mississippi, Arkansas, Louisiana, Oklahoma, and Texas (NatureServe 2018). NatureServe (2018) erroneously lists this species as presumed extirpated in Illinois. The State of Illinois lists

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this plant as endangered (Nÿboer & Ebinger 2004). With its thick rhizomes Vaccinium stamineum is very fire resistant and can form large thickets from resprouts. In most of its range, this species is not threatened but at its margins, such as southern Illinois, ecological conditions are marginal for its existence (Hill 2002a).

Deerberry had been presumed extirpated from Illinois until recently. Robert H. Mohlenbrock found the original site in 1962 at Double Branch Hole Ecological Area in Pope County, but it has not been relocated in subsequent searches. It was also found on the Forest in Hayes Creek Canyon on a south facing, sandstone ledge within the Double Branch Hole Ecological Area. It was last collected there in 1977. Later attempts to relocate this plant there were unsuccessful (Hill 2002a). Raymond G. Smith found a small population of this species in Hardin County within the Kaskaskia Experimental Forest on May 12, 1998. This occurrence, last observed at that location in 2015, is the only known extant site of deerberry in Illinois.

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