United States 

Department of 

Agriculture Rehabilitation of Alpine 

Forest Service Vegetation in the Adirondack 

NortheasternForest Mountains of New York State Experiment Station 

Research Paper 

N E-553 

1985 

E. H. Ketchledge 

P~=% R. E. Leonard @ N. A. Richards 

P. F. Craul 

A. R. Eschner 
The Authors 

E. H. Ketchledge is professor of forest botany; N. A. Richards is professor 

of forest ecology; P. F. Craul is professor of forest soils; and A. R. Eschner is 

professor of forest hydrology, State University of New York, Coltege of Environmental Science and Forestry, Syracuse, New York. R. E. Leonard is project 

leader, backcountry facilities, USDA Forest Service, Northeastern Forest 

Experiment Station, Durham, New Hampshire. 

Abstract 

Alpine communities of dwarf shrub and herbaceous vegetation in the 

Adirondack Mountains occur on only 20 isolated summits in the high peaks 

region. These limited communities, composed in part of rare northern species, 

are in danger of destruction from hiker trampling and subsequent erosion. On 

the two highest peaks, Mt. Marcy and Mt. Algonquin, much of the alpine 

communities immediately around the summits have already been lost. Unless 

corrective measures are taken, the remaining 40 acres of alpine vegetation 

may in time be lost. This paper describes field experiments in using sodforming grasses from lower elevations as soil stabilizers, and discusses the 

effects of fertilizing and transplanting native vegetation as part of an integrated management plan for rehabilitating alpine plant communities in the 

Adirondacks. Results show that it is possible to stabilize severely degraded 

alpine communities by seeding exposed humus and detritus with bluegrass 

(Poa pratensis L.) or red fescue (Festuca rubra L.) and fertilizing with a complete fertilizer and lime. When the treated areas are protected from further 

hiker impact, native vegetation returns; first a mat of mosses develops under 

the grasses, then seedlings or rhizomes of vascular plants slowly invade the 

site. 
Problem 

Alpine vegetation on Adirondack 

summits is fragile because of shallow, 

nutrient-poor soils, a short growing 

season, and harsh microclimatic conditions (Kalinowski 1983; Ketchledge 

1982; LeBlanc 1981; Cate 1974). The 

additional stress of trampling by 

hikers destroys vegetation and leads 

to erosion of the underlying organic 

soil mantle. The problem for land 

managers is to develop techniques to 

stabilize the eroding surfaces long 

enough for native plants to return, 

once human trespass is reduced. 

Background 

The Adirondack high peaks are 

formed from domes of anorthosite 

rock, which is highly resistant to 

weathering. Twenty peaks extend 

above timberline and support an 

alpine zone covering 83 acres; vascular plant communities occupy 41 

acres, with 1 acre or more on each of 

7 peaks and less than 1 acre on another 13 (DeNunzio 1972). These are 

local subclimax communities positioned on relatively smooth rock surfaces and exposed to severe climatic 

stresses. They are found on windswept/slopes with insufficient soil * 

depth to support trees. In contrast, 

the more protected surfaces of rock 

fissures and depressions support 

a krummholz community composed 

of black spruce (Picea mariana [Mill.] 

B.S.P.) and balsam fir (Abies balsamea 

[L.] Mill., dwarfed primarily by desiccating winter winds. In several cases, 

the krummholz occurs above timberline at elevations similar to or slightly 

higher than the alpine community on 

the same peaks, indicating the protective value of the winter snow fields 

on these summit islands (LeBlanc 

1981). 

The soil of the alpine plant community is essentially an unconsolidated organic mat overlying a thin 

layer of mineral grains formed by 

slow weathering of the parent material. The mat is composed of peat 

moss of great age, where vascular 

plants have rooted and now contribute 

their organic remains. The surface is 

stabilized by a plant community dominated by alpine bilberry (Vaccinium 

uliginosum L.), deer-grass (Scirpus 

caespitosus L.), black spruce, balsam 

fir, and lesser amounts of 93 other 

species of vascular plants (Ketchledge 

1984; Ketchledge and Leonard 1982; 

Phelps 1970). The soil can be described as a Lithic Borofolist (Soil 

Survey Staff 1975). (See Table 1.) 

The typical profile has an Oi layer 

of partially decomposed sphagnumwoody peat, held together by woody 

roots and buried stems. This overlies 

a greasy black humus Oa layer and 

the thin layer of leached, II C mineral 

grains just above bedrock. The minera1 layer presumably supplies small 

amounts of most essential nutrients 

except .nitrogen. The pH of the humus 

layer ranges around 3.8 while the 

bedrock is slightly acid to near neutral. The peat, lacking woody tissue, 

is highly susceptible to trampling 

under a range of moisture conditions. 

When near saturation, which is its 

moisture condition most of the year, 

the peat is easily deformed at the 

surface and crushing of the mat occurs along with mechanical damage 

to the vegetation. As the peat dries 

toward the end of summer, or during 

droughty periods, the peat becomes 

resilient and somewhat more resistant 

to crushing and compaction. However, the surface is extremely dry and 

scuffs easily and may even be blown 

away by the wind where it is bare of 

vegetation. The peat may also be dry 

in winter without snowcover, and is 

very susceptible to wind erosion. In 

cold weather, especially in late fall or 

early spring, only the surface may 

freeze to a depth of 2 to 3 cm. This 

Table 1.-Typical Lithic Borofolist profile description: Mt. Colden 

Horizon Depth (cm) Description - 

Oi 0-1 1 Light brown fibric material, Sphagnum 

spp., roots of grasses and alpine shrubs, 

15 percent coarse fragments, pH 3.9 

Oa 1 1-28 Black decomposed sapric material with 

10 percent anorthosite grains, fine sand, 

pH 3.8 

II C 28-29.5 Bleached anorthosite fine-to-medium sand 

grains, with some mixed sapric material, 

pH 4.0 

II R 29.5 Anorthosite bedrock, coarsely jointed and 

impermeable ' 

Range in characteristics: The observed soils may be as shallow as 9 cm, with 

each horizon reduced in thickness proportionately, and with less obvious 

development of the II C, which may be no more than a thin layer several grains 

in thickness. As the profile thickens, such as in fissures or bedrock depressions, the Oa thickens at a greater proportion than the other horizons. One 

profile had a thickness of 38 cm, and a clearly developed Oa horizon, absent in 

the shallower profiles. The Oa horizons appear to be near field capacity when 

observed :in the spring and fall; whereas the Oi may become quite dry in late 

summer, during winter when bare, or during periods of low rainfall. During 

heavy rains, water may be observed seeping from the lithic contact surface 

where a profile has been transversed by a hiking trail, or eroded away. 
Wlethods 

crust collapses under foot traffic, that larger segments are dislodged. 

shearing the frozen peat and any It is easy to see the greatly accelervegetative roots contained in it. Sub- ated damage to these high peaks 

sequent drying allows the sheared communities: the large bleached 

edge to collapse, increasing its sus- areas of recently exposed rock surceptibility to wind erosion. Hence, faces contrast markedly with the 

peat is a poor traffic surface in almost darker, lichen-covered surfaces that 

any condition. have been exposed for longer periods. 

Destruction of the plant-soil mat 

Unlike alpine meadows else- leaves a serviceable, indestructible 

where in the northeastern United rock surface for general recreation 

States, these communities contain purposes, but also creates less pleasfew sod-forming graminoids. The ant pockets of muck in depressions 

three most abundant native grasses, downslope. However, the primary 

boreal bentgrass (Agrosfis borealis resource problem is loss of the rare 

Hartm.), sweetgrass (Hierocloe alpina and delicate plant species found 

[Sw.] R&S), and alpine cottongrass nowhere else in the State of New 

(Eriophorum alpinum L.), are occa- York. 

sionally found on deeper soils but are 

all clump species and do not spread Trails through the atpine zone 

laterally to bind the soil matrix. Only are affected mainly by water and 

deer-grass (Scirpus caespitosus t.) traffic erosion. Gullies cut through 

and, to a lesse: extent, Bigelow's the deeper soil to bedrock and make 

sedge (Carex bigelowii Torr.) appear trails wet and mucky throughout most 

highly resistant to trampling by recre- of the hiking season. Darnage to 

ationists; indeed, these graminoids krummholz and meadow can be ametypically constitute the last surviving liorated by careful trail location and 

cover of vascular plants where human diversion of water from trails whenimpact is the greatest. ever possible. Similar problems on 

lower slopes are discussed elsewhere 

Once the plant cover is damaged by Ketchledge and Leonard (1970) 

by trampling, wind appears to be the and Ketchledge (1971; 1974). Presenrmajor destructive factor, killing stems ing alpine flora is more complex. 

and roots by desiccation and drying Stabilizing degraded soils is an inand eroding the peat and humus sur- tegral part of the sdution, and estabfaces. Traits quickly wear through the lishing sod-forming grasses from 

mat to bedrock. Thereafter, lateral lower elevations may be a useful 

undercutting by wind and water ex- management tool. 

pands the areas of destruction so 

Initial Work 

Mt. Dix, elevation 4,857 feet, has 

a narrow strip of alpine vegetation 

which has been seriously affected by 

the main trail over the summit. Efforts 

to rehabilitate this site began in 1967. 

First, clumps of native Agrostis borealis were transplanted to eroded peat 

areas and fertilized, but did very 

poorly. Small test plots of a standard 

lawn grass seed mixture with fertilizer 

were more successful. Further tests 

of grass seed and fertilizer were 

carried out over the following 2 years 

with promising results. The extreme 

acidity of the soil indicated that 

liming might be beneficial. Quicklime (hydrated lime) gave negative 

results, possibly because it was 

caustic to the plants or disrupted 

the CalMg balance in plant nutrition. 

All further tests used Mg-containing 

(dolomitic) agricultural ground limestone. These initial results suggested 

that grass species from lower elevations, supplemented with fertilizer 

and lime, would help to stabilize 

eroding areas and protect the native alpine community from further 

deterioration. 

Refinement of Techniques 

To refine this technique, test 

plots of various grass species and 

fertilizer combinations were established in June 1971. Mt. Colden, elevation 4,714 feet, with 0.6 acres of 

alpine meadow, was serected as the 
test area. Its summit vegetation had 

been seriously degraded by summitlounging and camping as well as by 

multiple trails. 

Fertilizer Tests 

A 1140-acre area was seeded to a 

mixture of 2 lb red fescue, 1 Ib Kentucky bluegrass, and % Ib redtop 

(Agrostis alba L.) (approximately 

equaf numbers of seeds from each 

species) and different combinations 

of fertilizer were applied. Results are 

summarized in Table 2. 

These results indicate that N is 

more limiting than P, that the source 

of N is not critical, and that K is beneficial but not critical. Limed areas 

were more successful than unlimed 

ones. The modest rate of liming probably affected the pH of the soil surface only, but may have also improved 

supplies of Ca and Mg as critical 

nutrient elements. 

Grass Species Tests 

Test plots of grasses were established on a 1120-acre area fertilized 

with 12-24-12, with half of each plot 

also limed. The species or varieties 

seeded were common Kentucky bluegrass, common red fescue, "Nugget" 

Kentucky bluegrass, and "Arctared" 

red fescue (both Alaskan varieties), 

"Highland" colonial bentgrass (Agrostis tenuis Sibth.) and common redtop. 

These species have been used successfully in arctic revegetation trials 

(Johnson and Van Kleve 1976). By the 

first autumn, the bluegiass and fescue 

plots were equally successful, with 

over 50 percent initial cover where 

limed and 10 percent cover where 

unlimed. They were generally unsuccessful on exposed peat surfaces 

which happened to occur mostly on 

the unlimed area. Both Agrostis species showed poorer take and initial 

growth. The plots were fertilized 

periodically between 1972 and 1980. 

By the end of the second growing 

season, both bluegrasses and fescues 

covered well where present, but areas 

of exposed peat remained unvegetated. Both Alaskan varieties showed 

slightly slower growth but greener 

color, suggesting better adaptation 

Table 2.-Effects of fertilizer treatments on grass establishment: Mt. Colden, 1971 

Treatment with grass Elemental rate Grass establishment 

seeding in June Ib per acre by September - 

Superphosphate 

with lime 

Superphosphate 

and Urea 

with lime 

Superphosphate 

Ammonium nitrate 

with lime 

with lime 

Failure 

Poor 

Satisfactory 

Good 

Satisfactory 

Good 

Good 

Best 

aLimed at 1000 lblacre ground dolomitic limestone. 

to the nutrient status of the site, 

with "Nugget" bluegrass particularly 

better adapted than the common 

variety. Patches of colonial bentgrass 

did well on more favorable microsites, 

while the redtop was sparse despite 

its reputation for tolerance of acidic, 

poorly-drained conditions. In September 1972, 10 permanent 50-cm-square 

plots were established throughout 

the seeded areas on Mt. Colden to 

monitor vegetation changes in greater 

detail. From periodic observations 

through 1980, it appears that the 

grasses are weakly holding where 

established; bluegrass in particular 

is showing some vegetative expansion. However, the area must be 

refertilized every few years to maintain the grass cover. 

The bluegrasses, and to a lesser 

extent the fescues, were heavily 

grazed during the second growing 

season (1979) and thereafter, predominantly by varying hare (Lepus 

arnericanus Eryleben). However, cclonial bentgrass, which has an agricultural reputation for low palatability, 

was not grazed and consequently 

reached full development and flowering. Concern that this selectivity 

might permit the relatively tall bentgrass to spread too aggressively has 

proven unfounded, as the species has 

not advanced beyond its initial areas 

of establishment. Closer examination 

of the native shrubs showed a history of browsing also. Thus herbivore 

food habits must be considered a 

controlling factor in the natural growth 

of these alpine communities, and may 

be a selective factor in determining 

species composition also. The varying hares move from the spruce-fir 

forest and the krummholz transition 

zone into the open summit areas to 

feed during the summer season. 

Grazing provides regular mowing of 

the introduced grass, keeping it in 

scale with the natural dwarf flora 

and, incidentally, providing a pleasant 

recreational surface for the human 

visitors. However, in ecological terms, 

the attraction of succulent, highnutrient grass could have other consequences. Either grazing of grass 

could take pressure off native vegetation as a food source or it could support a larger herbivore population to 

feed on native flora when the grass is 

dormant or snow-covered. The impact 

of herbivores needs further study. 

Vegetational Dynamics 

Annual monitoring of all test 

sites reveals three phases in the 

recovery process of treated areas: 

First, it takes three seasons 

to develop a continuous cover of 

grasses, because of such environ- 
mental hazards as loss of seed from 

the site by wind removal or bird depredation. If the annual fertilizer and lime 

treatment is discontinued after the 

third season, the introduced grasses 

go into a gradual decline lasting 3 to 

6 years, depending upon the intensity 

of initial treatment. 

Second, as the vigor of the grasses 

declines in succeeding seasons, native vascular plants from healthy 

nearby stands do not invade the 

treated sites; rather, the native bryophytes, primarily mosses, become 

established. Most important, Pohlia 

nutans [Hedw.] Lindb., a common 

cushion moss throughout the northern 

forest region, invades the treated 

sites, and within a few seasons forms 

a continuous cover wherever the site 

was previously fertilized. Various 

other native mosses, liverworts, and 

lichens, about a dozen species in all, 

soon invade and dominate the site 

as the grasses wither away. 

Third, few vascular plants appear 

able to invade the treated sites successfully until the surface is covered 

by a carpet of mosses. The first vascular plant to pioneer the moss cover 

is the mountain sandwort Arenaria 

groenlandica [Rets.] Spend., which 

invades by seedlings; it is followed 

a season or so later by vegetation 

spread onto the site by rhizomes of 

several native plants, particularly 

Bigelow's sedge and the three-tooth 

cinquefoil (Potentilla tridentata Solender ex Ait.) Within a few seasons, 

either seedlings or sprouts of numerous alpine natives reappear on the 

treated sites in low numbers, including 

both such floristic rarities as the fir 

clubmoss (Lycopodium selago L.) 

and the vegetatively dominant alpine 

bilberry. 

Although establishment of a 

moss cover is vigorous and relatively 

rapid over a 4- or 5-year period, the 

return of vascular plants is very slow, 

even on areas that have received additional treatment with lime and fertilizer. Where undisturbed by hiker 

traffic, the moss carpet appears to 

thicken at the rate of approximately 

half an inch a season; by contrast, 

vascular plants appear at a rate of 

only one to two seedlings or sprouts 

per square foot of surface per year. 

The continuous carpet of moss, if 

protected from human impact, appears resistent to both water and 

wind erosion, but the reestablishment 

of thevascular plant community must 

be measured in decades rather than 

years. 

Where not protected from hikers, 

the new moss carpet may be destroyed within a single season, as 

seen in the main trail over the crest of 

Mt. Dix where we began our tests in 

1967. Recovered vegetation on either 

side of the trail itself, however, appeared to hold its own. When the 

moss carpet is broken by hiker impact, it is lifted and destroyed by 

winds, and site erosion resumes. The 

mosses therefore appear to be more 

persistent and better adapted to the 

natural site conditions of the summits 

than the planted grasses, but less 

resistant to hiker impacts. Similarly, 

on Algonquin Peak, where the main 

trail has been rerouted onto the rocks, 

the treated damaged areas have responded vigorously and appear well 

on the way to recovery as a stable 

community. 

Treatment of Other Summits 

From these test plot results, a 

standard treatment was developed 

for use on other deteriorating alpine 

areas on Adirondack summits: 

-Kentucky bluegrass (preferably 

"Nugget"): 1 lbl20 milacres (870 

sq ft) or bluegrass % Ib plus red 

fescue 1/2 lbl20 milacres 

-Fertilizer at 20 lbl20 milacres 

12-24-12 or equivalent rate 

-Dolomitic (CalMg) agricultural 

ground limestone 40 lb120 milacres 

(1 tonlacre) 

-Refertilization on the following year 

and every few years thereafter 

This treatment has been applied 

annually to eroding alpine areas on 

five other Adirondack peaks over a 

12-year period by volunteers from the 

Adirondack Mountain Club, the Adirondack Fortysixers, and students 

from the New York State Ranger 

School. In general, alpine areas in 

early stages of damage have been 

stabilized in a few years of treatments, but areas with more extensive 

vegetation destruction and erosion 

have required repeated treatments 

for several years to stabilize the soil 

(Ketchledge and Leonard 1971, 1972; 

Ketchledge 1973a, 19734 1975). 
Conclusion 

Rehabilitation of denuded sites 

by the use of sod-forming grasses 

may be a useful initial measure to 

halt degradation of alpine plant communities in the Adirondacks. However, this method must be combined 

with user management and education 

to solve the problems of hiker impact 

on these inherently fragile areas. 

The success of grass establishment depends upon the substrate, as 

is illustrated by a typical cross-section 

of the disturbed community (Fig. 1). 

Low-elevation, sod-forming grasses 

are generally effective in covering and 

stabilizing exposed or accumulated 

humus along trail edges and other 

damaged areas. They have not proven 

as effective in colonizing exposed 

peat, however; the seedlings apparently are unable to grow vigorously in 

such a nutrient-poor medium and extreme microclimate. When well established on humus, though, grass 

provides effective protection along 

trails and "lounging areas" during 

the summer and early fall. The introduced grass can be damaged easily 

in early spring when the soil is waterlogged and grass cover is weakest. 

The experience .of 12 seasons on 

Algonquin Peak shows that grass 

may be maintained for several years 

only if fertilized annually. Without 

treatment, the grass withers and is 

soon replaced by a continuous carpet 

of mosses that is only slowly replaced 

by native vascular plants. The grass 

cannot withstand heavy recreational 

traffic, nor campfires occasionally 

built by some thoughtless visitors. 

Accordingly, the restoration of summit 

vegetation must be viewed as only 

one step in an integrated summit 

management program aimed primarily 

at directing the flow of visitors off the 

meadows and out onto the resistant 

rock surfaces. Most important, the 

trail path itself must be built up with 

native rocks to provide a stone pathway wherever it is impossible to reroute the trail over the bedrock; this 

procedure has been most successful 

on Algonquin Peak where the Conservation Department summer rangers 

have constructed three such pathways across sections of delicate 

alpine meadow. Similarly, we have 

overcome wind erosion on various 

exposed sites by packing loose rocks 

on the bare humus banks and then 

treating the edges with seed, lime, 

and fertilizer as on flat surfaces of 

damaged meadow. 

Management of hiker traffic, 

using such methods as rerouting 

trails over bare rock, marking trails 

clearly to avoid widespread wandering, and discouraging camping above 

timberline, is necessary to prevent 

degradation on any high summit. 

Education of the hiking public must 

be a key element in resource management; in general, the public is 

amenable to restrictions when it understands the reasons behind them. 

Similarly, updated recreational practices should be stressed; camping 

stoves, for example, should replace 

open wood fires. 

Figure 1.-Typical cross-section of disturbed community. 

A. Undercut trail edge: Continuing deterioration of trail edge and adjacent vegetation. 

B. Trail edge with exposed humus (Oa): Grass established easily in humus, stabilizes 

edge and is quite resistant to trampling. 

C. Exposed peat (Oi): Grass establishment very slow, requiring repeated treatment. 

Moss cover more readily established, effective for site protection but vulnerable to 

hiker damage. Little recovery of severely damaged shrubs. 

D. Humus accumulation in hollow: Grass establishment rapid and effective, except in 

very wet bottom of hollow. Occasional reestablishment of alpine herbs, especially 

mountain sandwort and three-toothed potentilla. 

E. Edge of less-damaged shrubs or krummholz: Grass establishment effectively protects 

edge from further deterioration. Shrubs may show some growth in response to 

fertilizer. 
In 1980, the Department of Environmental Conservation inaugurated 

a policy prohibiting overnight camping 

above 4,000 feet elevation in the 

Adirondacks, as recommended by 

recreational leaders (Ketchledge 1977, 

1979). New generations of recreationists seeking "pioneering" experiences 

and lacking ecological sensitivity, 

however, make continuing educational 

efforts necessary. Inviting volunteer 

efforts by hikers to rehabilitate such 

areas may have positive results beyond the economic and labor savings, 

by devebping their awareness and 

acceptance of management techniques and the basic problems of 

human impact on such rare and fragile 

areas. 

Literature Cited 

Cate, David. A fragile world. Adirondack Life. 9(4):28-33; 1974. 

DeNunzio, M. A vegetational survey of 

the alpine zone of the Adirondack 

Mountains, New York State. Syracuse, NY: State University of New 

York College of Environmental 

Science and Forestry; 1972. M.S. 

thesis. 

Johnson, t.; Van Kleve, K. Revegetation in arctic and subarctic North 

America-a literature review. Hanover, NH: Cold Regions Research 

and Engineering Laboratory; 1976. 

Kalinowski, Thomas. New York's 

tundra. The Conservationist. 37(4): 

22-27; 1983. 

Ketchledge, Edwin H. Facility rehabil. 

itation. In: Recreation symposium 

proceedings; 1971 October 12-14; 

Syracuse, NY. Upper Darby, PA: 

U.S. Department of Agriculture, 

Forest Service, Northeastern Forest 

Experiment Station; 1971:166-172. 

Ketchledge, E. H. Progress report, 

high peak erosion studies, 1973. 

Adjrondack Peakks, 1!3(1):8-9; 1973a. 

Ketchfedge, E. H. Erosion study, fall 

1973. Adirondack Peaks. 10(2]:2-3; 

1973b. 

Ketchledge, E. H. The Adirondack high 

country: Its ecology and conservation. In: Proceedings, sportsmen's 

conservation workshop; (dates unknown); Ithaca, NY: Cornell University, Department of Natural 

Resources, New York State College 

of Agriculture and Life Sciences; 

1974:68-74. 

Ketchledge, E. H. Progress report, 

high peak erosion studies, 1975. 

Adirondack Peaks. 12(1):26-28; 

1975. 

Ketchledge, E. H. Summit deterioration-the alpine zone. In: High 

peaks wilderness advisory committee summary findings report. 

Albany, NY: New York State Department of Environmental Conservation; 1977:16. 

Ketchledge, E. H. Flora endangerment 

of the high peaks. In: 9th conference 

on the Adirondack Park; 1979 June 

7-9. Canton, NY: St. Lawrence University; 1979:43-47. 

Ketchledge, E. H. The sensitive summits. Adirondac. 46(6):20-21; 1982. 

Ketchledge, E. H. The alpine flora. 

Adirondac. 48(5):17-20; 1984. 

Ketchledge, E. H.; Leonard, R. E. The 

impact of man on the Adironda~k 

high country. The Conservationist. 

25(2):14-18; 1970. 

Ketchiedge, E. H.; Leonard, R. E. Prog. 

ress report, high peaks erosion 

studies. Adirondack Peaks. 8(2): 

8-10; 1971. 

Ketchledge, E. H.; Leonard, R. E. Prog. 

ress report, high peaks erosion 

studies, 1972. Adirondack Peaks. 

9(1):12-13; 1972. 

Ketchledge, E. H.; Leonard, R. E. Summit stability. Adirondac. 46(10): 

22-23; 1982. 

LeBlanc, D. C. Ecological studies on 

the alpine vegetation of the Adirondack Mountains of New York. 

Plattsburg, NY: State University of 

New York; 1981. M.S. thesis. 

Phelps, Orra. Mountaintop flora. In: 

The Adirondack high peaks and the 

forty-sixers. Adirondack, NY: The 

Adirondack Fortysixers; 1970 

275-290. 

Soil Survey Staff. Soil taxonomy. 

Agric. Handb. 436. Washington, DC: 

U.S. Department of Agriculture, Soil 

Conservation Service; 1975. 754 p. 
Ketchledge, E. H.; Leonard, R. E.; Richards, N. A.; Craul, P. F.; 

Eschner, A. R. Rehabilitation of alpine vegetation in the 

Adirondack Mountains of New York State. Research Paper 

NE-553. Broomall, PA: U.S. Department of Agriculture, Forest 

Service, Northeastern Forest Experiment Station; 1985. 6 p. 

This paper describes field experiments in using sod-forming 

grasses from lower elevations as soil stabilizers, and discusses 

the effects of fertilizing and transplanting native vegetation as 

part of an integrated management plan for rehabilitating alpine 

plant communities in the Adirondacks. Results show that it 

is possible to stabilize severely degraded alpine communities 

by seeding exposed humus and detritus with bluegrass (Poa 

pratensis L.) or red fescue (Festuca rubra L.) and fertilizing 

with a complete fertilizer and lime. When the treated areas are 

protected from further hiker impact, native vegetation returns; 

first a mat of' mosses develops under the grasses, then seedlings 

or rhizomes of vascular plants slowly invade the site. 

ODC 907.32 

Keywords: alpine rehabilitation; fertilization. 

a US. GOVERNMENT PRINTING OFFICE: 1985-505-0281537 
Headquarters of the Northeastern Forest Experiment Station are in 

Broomall. Pa. Field laboratories are maintained at: 

Amherst, Massachusetts, in cooperation with the University of 

Massachusetts. 

0 Berea, Kentucky, in cooperation with Berea College. 

Burlington, Vermont, in cooperation with the University of 

Vermont. 

0 Delaware, Ohio. 

0 Durham, New Hampshire, in cooperation with the University of 

New Hampshire. 

Hamden, Connecticut, in cooperation with Yale University. 

Morgantown, West Virginia, in cooperation with West Virginia 

University, Morgantown. 

Orono, Maine, in cooperation with the University of Maine, 

Orono. 

Parsons, West Virginia. 

Princeton, West Virginia. 

Syracuse, New York, in cooperation with the State University of 

New York College of Environmental Sciences and Forestry at 

Syracuse University, Syracuse. 

0 University Park, Pennsylvania, in cooperation with the 

Pennsylvania State University. 

0 Warren, Pennsylvania.