|
Wildlife, Animals, and Plants
|
|
Introductory
SPECIES: Lycium berlandieri | Berlandier Wolfberry
ABBREVIATION :
LYCBER
SYNONYMS :
NO-ENTRY
SCS PLANT CODE :
LYBE
COMMON NAMES :
Berlandier wolfberry
wolfberry
desert thorn
squawberry
TAXONOMY :
The currently accepted scientific name of Berlandier wolfberry is Lycium
berlandieri Dunal. (Solanaceae) [23,31,41]. A typical variety and L. b.
var parviflorum (Gray) Terrac. are recognized by some authors [23,31].
Vines [41] also recognizes L. b. forma parviflorum (Gray) Hitchc., L. b.
var. longistylum Hitchc., and L. b. var. brevilobum Hitchc.
LIFE FORM :
Shrub
FEDERAL LEGAL STATUS :
No special status
OTHER STATUS :
NO-ENTRY
COMPILED BY AND DATE :
Robin F. Matthews, May 1994
LAST REVISED BY AND DATE :
NO-ENTRY
AUTHORSHIP AND CITATION :
Matthews, Robin F. 1994. Lycium berlandieri. In: Remainder of Citation
DISTRIBUTION AND OCCURRENCE
SPECIES: Lycium berlandieri | Berlandier Wolfberry
GENERAL DISTRIBUTION :
Berlandier wolfberry ranges from Arizona to Texas and south into Mexico
[23,31,41]. Lycium berlandieri var. berlandieri is common in southern
Texas and is distributed from southern and western Texas to central
Mexico. Lycium b. var. parviflorum is more common in the Trans-Pecos
than the typical variety and is distributed from Arizona to western
Texas and south to northern Mexico [31]. Lycium b. f. parviflorum
occurs in Arizona and Mexico, L. b. var. longistylum is from southern
Arizona, and L. b. var. brevilobum occurs in Texas and Mexico [41].
ECOSYSTEMS :
FRES28 Western hardwoods
FRES30 Desert shrub
FRES32 Texas savanna
FRES33 Southwestern shrubsteppe
FRES38 Plains grasslands
FRES39 Prairie
FRES40 Desert grasslands
STATES :
AZ NM TX MEXICO
ADMINISTRATIVE UNITS :
BIBE GUMO ORPI SAGU
BLM PHYSIOGRAPHIC REGIONS :
7 Lower Basin and Range
12 Colorado Plateau
13 Rocky Mountain Piedmont
14 Great Plains
KUCHLER PLANT ASSOCIATIONS :
K027 Mesquite bosque
K040 Saltbush - greasewood
K041 Creosotebush
K042 Creosotebush - bursage
K043 Paloverde - cactus shrub
K044 Creosotebush - tarbush
K045 Ceniza shrub
K053 Grama - galleta steppe
K054 Grama - tobosa prairie
K058 Grama - tobosa shrubsteppe
K059 Trans-Pecos shrub savanna
K060 Mesquite savanna
K061 Mesquite - acacia savanna
K062 Mesquite - live oak savanna
K065 Grama - buffalograss
K076 Blackland prairie
K077 Bluestem - sacahuista prairie
SAF COVER TYPES :
68 Mesquite
235 Cottonwood - willow
241 Western live oak
242 Mesquite
SRM (RANGELAND) COVER TYPES :
NO-ENTRY
HABITAT TYPES AND PLANT COMMUNITIES :
Berlandier wolfberry occurs in many habitats but usually does not attain
dominance. It is characteristic of Sonoran or Chihuahuan desert scrub
vegetation and is associated in those regions with ocotillo (Fouquieria
splendens), saguaro (Carneigea gigantea), range ratany (Krameria
parvifolia), ironwood (Olneya tesota), jojoba (Simmondsia chinensis),
false-mesquite (Calliandra eriophylla), brittle bush (Encelia farinosa),
leatherstem (Jatropha cardiophylla), feather dalea (Dalea formosa),
yucca (Yucca spp.), agave (Agave spp.), prickly pear and cholla (Opuntia
spp.), and catclaw (Acacia spp.) [3,10,30,35,37]. In the Chihuahuan
Desert, Berlandier wolfberry may also occur in alkali sacaton
(Sporobolus airoides) grasslands on deep calcareous alluvial deposits
near arroyos and in intermontane habitats along the margins of honey
mesquite (Prosopis glandulosa var. glandulosa) communities [20].
In southern Texas Berlandier wolfberry is associated with hackberry
(Celtis spp.), prickly pear, catclaw, bluewood (Condalia obovata), Texas
persimmon (Diospyros texana), lotebush (Zizyphus obtusifolia),
whitebrush (Aloysia lyciodies), agrito (Mahonia trifoliolata), desert
yaupon (Schaefferia cuneifolia), curlymesquite (Hilaria belangeri),
tobosa (Hilaria mutica), grama (Bouteloua spp.), and dropseed
(Sporobolus spp.) [8,24,28]. Mesquite-hackberry (Celtis
spp.)-Berlandier wolfberry communities are most common on smaller
drainages within sandy areas where soil textures are sandy loams, and
along edges of saline waterways near the coast [28].
Berlandier wolfberry also occurs in openings in riparian or arroyo
margin woodlands dominated by Arizona sycamore (Platanus wrightii),
Fremont cottonwood (Populus fremontii), green ash (Fraxinus
pennsylvanica), Goodding willow (Salix gooddingii), and saltcedar
(Tamarix chinensis) [29,30].
VALUE AND USE
SPECIES: Lycium berlandieri | Berlandier Wolfberry
WOOD PRODUCTS VALUE :
NO-ENTRY
IMPORTANCE TO LIVESTOCK AND WILDLIFE :
Berlandier wolfberry fruits are important food for birds and some
rodents [39]. Livestock may browse Berlandier wolfberry foliage
[23,31]; however, it was available on southern Texas plains but was not
reported in cattle diets [11]. Black-tailed jackrabbit winter diets in
southern Texas consisted of 3 percent Berlandier wolfberry [40].
In southern Arizona Gambel's quail were closely tied to habitats
characterized by mesquite (Prosopis spp.), netleaf hackberry (Celtis
reticulata), falsemesquite, and Berlandier wolfberry along sandy washes
or around stock tanks. There was an average of 60 Berlandier wolfberry
plants per 0.4 hectare plot in areas most used. Gambel's quail used
Berlandier wolfberry for cover, roosting and feeding sites, and for
raising broods. These habitats were also important for introduced
masked bobwhites when preferred habitat was limited. There was an
average of 83 Berlandier wolfberry plants per 0.4 hectare plot in scaled
quail habitat found in adjacent grasslands dominated by low grasses,
broom snakeweed (Gutierrezia sarothrae), and Berlandier wolfberry.
Scaled quail used Berlandier wolfberry for hiding cover and preferred
plants 1.7 to 5.0 feet (0.5-1.5 m) tall for loafing cover [16].
PALATABILITY :
NO-ENTRY
NUTRITIONAL VALUE :
NO-ENTRY
COVER VALUE :
NO-ENTRY
VALUE FOR REHABILITATION OF DISTURBED SITES :
Specific information regarding the use of Berlandier wolfberry for
rehabilitating disturbed sites is not available in the literature.
Wolfberries (Lycium spp.), however, have been used to rehabilitate
abandoned farmlands in Sonoran Desert lowlands and on disturbed sites
near Red Rock, Arizona. The sites were restored by establishing berms
on the contour and then seeding with wolfberry and other desert shrubs
[22].
OTHER USES AND VALUES :
Historically, Native Americans have eaten Berlandier wolfberry berries
and have used the plant for a wide variety of medicinal purposes [23,31].
MANAGEMENT CONSIDERATIONS :
Berlandier wolfberry had a frequency of 0.4 percent on sites protected
from livestock grazing for 50 years at the Desert Labratory near Tucson,
Arizona. It was not present on unprotected sites, but the differences
were not significant [3].
Woody species such as Berlandier wolfberry often invade grasslands and
reduce the amount of valuable forage. Fall aerial applications of
picloram, 2,4,5-T, or a mixture of the two were relatively ineffective
for control of Berlandier wolfberry in southern Texas [5]. However,
aerial applications of tebuthiuron were effective in killing all
Berlandier wolfberry plants within 1 year on a 130-acre (52-hectare)
study plot on the Jornada Experimental Range, New Mexico [14].
BOTANICAL AND ECOLOGICAL CHARACTERISTICS
SPECIES: Lycium berlandieri | Berlandier Wolfberry
GENERAL BOTANICAL CHARACTERISTICS :
Berlandier wolfberry is a spiny shrub up to 7 feet (2 m) tall with few,
spreading branches. The axillary flowers are bell-shaped and are borne
singly or in clusters. The fruit is a red juicy berry with 8 to 30
seeds [41]. Berlandier wolfberry sheds its leaves and becomes dormant
during drought but quickly refoliates when conditions are more favorable
[23]. Berlandier wolfberry is long-lived, with an average life span of
about 90 years [35]. Individuals of at least 72 years of age have been
observed at the Desert Labratory near Tucson, Arizona [15].
The roots of wolfberry species are tough and fibrous. Root systems are
relatively extensive in comparison with the aerial portions, often
extending 25 to 30 feet (7.5-9.0 m) from the plant [39].
RAUNKIAER LIFE FORM :
Phanerophyte
REGENERATION PROCESSES :
Berlandier wolfberry regenerates from cuttings, root suckering, and
layering [41]. It may also sprout from the base when damaged [41].
Berlandier wolfberry seeds are dispersed by birds and other animals [27].
Good seed crops are produced by wolfberry species almost every year.
After extraction, seeds should by dried and stored in sealed containers
at 41 degrees Fahrenheit (5 deg C), or stratified in moist sand.
Stratified seeds of other wolfberry species maintain good viability for
6 months. Dormancy in wolfberry seeds is variable. Some wolfberries
germinate well without pretreatment, while germination of others was
improved by stratification. Seeds can be sown in the fall as soon as
the fruits ripen, or stratified seed can be sown in the spring and
covered lightly with about 0.25-inch (0.64-cm) of soil. Two-year-old
seedlings may be outplanted [34].
SITE CHARACTERISTICS :
Berlandier wolfberry is found on flats, along washes or arroyos, on dry,
gravelly to sandy hills and bajadas, and on rocky slopes [6,23,31,30].
It also grows on or around saline flats or playas in the Chihuahuan
Desert, but is not restricted to such sites [19,28]. Berlandier
wolfberry is generally found at elevations up to 3,000 feet (900 m) in
Arizona and Texas [23,41] but occurs from 2,100 to 4,600 feet (636-1,400
m) elevation in the Trans-Pecos region [31].
SUCCESSIONAL STATUS :
On the Rio Grande Plains of southern Texas, succession may proceed from
grassland or savanna to closed canopy shrublands or woodlands. Mesquite
(Prosopis spp.) generally invades the grasslands or savanna initially,
and may act as a nurse tree for the establishment of other woody
species. Mesquite and the nursed plants form discrete clusters.
Berlandier wolfberry establishes in these clusters about 45 to 52 years
after initial establishment of mesquite. The clusters eventually become
continuous and form a closed canopy [1,2]. Berlandier wolfberry is
found in mesic mesquite-hackberry shrublands that are considered climax
associations on certain sites in southern Texas [28].
SEASONAL DEVELOPMENT :
Berlandier wolfberry flowers from March to September in Arizona [23] and
from February to October in the Trans-Pecos region [31]. It flowered in
October after fall rains in the lower Rio Grande Valley, Texas [42].
FIRE ECOLOGY
SPECIES: Lycium berlandieri | Berlandier Wolfberry
FIRE ECOLOGY OR ADAPTATIONS :
Berlandier wolfberry sprouts from the root crown following fire [17,26],
but it may take many years to regain its former density on a burned site
[33]. Its sprouting ability is most likely dependent on fire severity.
Wolfberry species seedling establishment was noted after a fire at a
Sonoran Desert site. The seeds may have survived the fire in the soil
or on burned plants, or may have been dispersed from adjacent unburned
areas [33]. Large clumps of woody species in southern Texas chaparral
communities do not burn completely. Fire-caused mortality in clumps not
mechanically treated was greatest on the windward side. Recurring fires
may have eliminated individual plants and small clumps but allowed
larger clumps to survive [7].
POSTFIRE REGENERATION STRATEGY :
Tall shrub, adventitious-bud root crown
Secondary colonizer - off-site seed
FIRE EFFECTS
SPECIES: Lycium berlandieri | Berlandier Wolfberry
IMMEDIATE FIRE EFFECT ON PLANT :
Severe fires may kill Berlandier wolfberry but low- to moderate-severity
fires probably only consume its aerial portions. Many small Berlandier
wolfberry plants were "completely destroyed" by a fire in savanna
vegetation in southern Texas [7].
DISCUSSION AND QUALIFICATION OF FIRE EFFECT :
NO-ENTRY
PLANT RESPONSE TO FIRE :
Berlandier wolfberry frequency was significantly (p<.01) reduced
following a fall prescribed fire at the Welder Wildlife Foundation
Refuge in southern Texas. Prefire frequency was 15 percent while
frequency in postfire year 1 was 4 percent. Postfire canopy cover was
83 percent less than prefire cover. The area was dominated by mesquite
(Prosopis glandulosa), huisache (Acacia farnesiana), and seacoast
bluestem (Schizachyrium scoparium var. littoralis) and had been
pretreated with shredding, chopping, or scalping 2 years earlier to
produce fuel sufficient for a uniform burn. There was significantly
(p<.05) less brush cover on pretreated than on untreated sites.
Berlandier wolfberry had the following percent canopy cover in postfire
year 1 under the different treatments [7]:
Treatment Burned Unburned
__________________________________________________________
Control 0.1 0.5
Shredded Trace 0.2
Chopped Trace 0.1
Scalped Trace 0.2
Brush canopy reduction, including that of Berlandier wolfberry, was
greatest at this site when treated plots were burned in the fall or
winter of 2 successive years, rather than once [8].
On the Rio Grande Plains of southern Texas, buffelgrass (Cenchrus
ciliaris) pastures have been invaded by woody species such as mesquite
(Prosopis spp.), blackbrush acacia (Acacia rigidula), twisted acacia (A.
tortuosa), Berlandier wolfberry, and others. Two cool-season prescribed
fires were applied to a buffelgrass pasture, one in February 1977 and
one in February 1979, to control woody species invasion. Both fires
reduced brush species to ground level. However, the suppression of
growth was short-lived and canopy diameters (including that of
Berlandier wolfberry) had recovered to prefire levels by the end of the
first growing season following the initial fire. Mortality was
insignificant even after the second fire. The fires did allow a
cumulative increase in forage production of buffelgrass for up to three
postfire growing seasons [17,18].
Wolfberry species sprouted rapidly after controlled June fires in
Sonoran desert scrub vegetation near Phoenix, Arizona. The
well-developed wolfberry root systems escaped damage from the fire,
allowing them to capitalize on increased water and nitrogen availability
in the postfire environment. Wolfberries had established their former
density and cover by 35 postfire months. Wolfberry plants had similiar
responses in both open shrub and tree microhabitats [26].
Wolfberry species sprouted and seedlings established within 3 years
following a June wildfire in a Sonoran Desert scrub community near
Phoenix, Arizona. No information was given on fire severity or
intensity [33].
DISCUSSION AND QUALIFICATION OF PLANT RESPONSE :
NO-ENTRY
FIRE MANAGEMENT CONSIDERATIONS :
Box and White [8] recommended fire for controlling woody species on
southern Texas savanna communities dominated by mesquite (Prosopis
glandulosa), huisache, and seacoast bluestem. Fall and winter burning
effectively reduced brush canopy and frequency, although fall burning
was slightly more effective. Fire was not particularly useful unless
sites had been mechanically pretreated to create a uniform fuel bed.
Best results are probably obtained by waiting a sufficiently long time
following mechanical treatment for crushed woody fuel to dry and a crop
of herbaceous species to mature among the woody debris.
Frequent fires in mesquite-hackberry-Berlandier wolfberry communities on
southern Texas plains may convert the vegetation to seacoast
bluestem-brownseed paspalum (Paspalum plicatulum)-balsamscale (Elyonurus
tripsacoides) associations [28].
Fires are not prevalent in many desert communities due to wide spacing
between shrubs and sparse ground cover [9,21]. Unusually heavy winter
rains, however, may produce a cover of annual species dense enough to
carry a fire when cured [21]. Many perennial desert shrubs are poorly
adapted to fire [9]. Postfire recolonization by long-lived desert
shrubs is very slow initially and may take hundreds of years [9,33].
Rogers and Steele [33] suggested a conservative approach when using fire
to manage desert regions.
FIRE CASE STUDIES
SPECIES: Lycium berlandieri | Berlandier Wolfberry
CASE NAME :
Fire temperatures and the effect of burning on south Texas brush communities
REFERENCE :
White, R. A. 1969 [44]
SEASON/SEVERITY CLASSIFICATION :
March/variable
STUDY LOCATION :
The study plot was located in Section 40, lots 7 and 8 of the Welder
Wildlife Foundation Refuge which is approximately 20 miles north of
Corpus Christi, Texas.
PREFIRE VEGETATIVE COMMUNITY :
The regional vegetation of the area was described as Gulf prairies and
marshes. Plant communities in the study area were dominated by mesquite
(Prosopis glandulosa), huisache (Acacia farnesiana), and seacoast
bluestem (Schizachyrium scoparium var. littoralis). Other woody species
present included Berlandier wolfberry (Lycium berlandieri), lotebush
(Zizyphus obtusifolia), blackbrush acacia (Acacia rigidula), twisted
acacia (A. tortuosa), agarito (Mahonia trifoliolata), Texas persimmon
(Diospyros texana), and hackberry (Celtis spp).
TARGET SPECIES PHENOLOGICAL STATE :
Berlandier wolfberry possessed a full complement of leaves at the time
of burning and 2 weeks following burning.
SITE DESCRIPTION :
NO-ENTRY
FIRE DESCRIPTION :
A prescribed fire was applied to a 10 acre (4 hectare) plot. One
portion was burned March 8, 1968; the rest was burned March 12,
1968. The following conditions were recorded at the time of burning:
Date Burned
Condition 3/8/68 3/12/68
______________________________________________________________________
Time of burning 3:00-3:30 pm 10:00 am-4:00 pm
Air temperature (deg F) 60 55
Relative humidity (%) 90 45
Wind velocity (mph) 10 20-30
Soil moisture (%) 40 37
Plant moisture (%) 9 7
Average height of flames (ft) 7 8
In subunit 1, the fuel was evenly distributed and high in loading, and
the brush was generally open. Subunit 2 had an uneven fuel
distribution, fuel loading was moderate, and brush was dense. There was
a low amount of evenly distributed fuel in subunit 3, and brush cover
was open.
FIRE EFFECTS ON TARGET SPECIES :
The canopy cover of all woody species, including Berlandier wolfberry,
was reduced by burning. Overall mortality of Berlandier wolfberry was
8 percent. Berlandier wolfberry had the following percent canopy cover
before and 3 months after the fire:
Percent Canopy Cover
Subunit Fuel load Prefire Postfire
--------------------------------------------------------------------------
Subunit 1 (3,686 lbs/acre) trace trace
Subunit 2 (1,932 lbs/acre) trace 1
Subunit 3 (1,970 lbs/acre) 1 trace
The extent of topkill and mortality of Berlandier wolfberry seemed to
increase with increasing fuel loads, but differences were not
statistically significant (p>.10). Overall brush mortality was
significantly (p<.01) higher in subunit 1, where fuel loadings were
highest. In subunit 2, where brush cover was dense, the fire was severe
enough to damage brush at the edges of clumps and significantly (p<.05)
reduce overall brush cover. In subunit 3, with low fuel loads and open
cover, brush cover was not significantly (p>.10) reduced.
FIRE MANAGEMENT IMPLICATIONS :
Overall, fire was an effective method for topkilling woody species but
did not result in high mortality. Low mortality may have been due to
high soil moisture and relatively low air temperatures. Under these
conditions, fire would have to be applied several times over a period of
years to kill many woody species. Maximum mortality may be obtained by
burning when woody plants are small and fuel quantities are high.
REFERENCES
SPECIES: Lycium berlandieri | Berlandier Wolfberry
REFERENCES :
1. Archer, Steve. 1989. Have southern Texas savannas been converted to
woodlands in recent history?. American Naturalist. 134(4): 545-561.
[10069]
2. Archer, Steve; Scifres, Charles; Bassham, C. R.; Maggio, Robert. 1988.
Autogenic succession in a subtropical savanna: conversion of grassland
to thorn woodland. Ecological Monographs. 58(2): 111-127. [10070]
3. Blydenstein, John; Hungerford, C. Roger; Day, Gerald I.; Humphrey, R.
1957. Effect of domestic livestock exclusion on vegetation in the
Sonoran Desert. Ecology. 38(3): 522-526. [4570]
4. Bernard, Stephen R.; Brown, Kenneth F. 1977. Distribution of mammals,
reptiles, and amphibians by BLM physiographic regions and A.W. Kuchler's
associations for the eleven western states. Tech. Note 301. Denver, CO:
U.S. Department of the Interior, Bureau of Land Management. 169 p.
[434]
5. Bovey, R. W.; Baur, J. R.; Morton, H. L. 1970. Control of huisache and
associated woody species in south Texas. Journal of Range Management.
23(1): 47-50. [10289]
6. Bowers, Janice E.; McLaughlin, Steven P. 1987. Flora and vegetation of
the Rincon Mountains, Pima County, Arizona. Desert Plants. 8(2): 50-94.
[495]
7. Box, Thadis W.; Powell, Jeff; Drawe, D. Lynn. 1967. Influence of fire on
south Texas chaparral communities. Ecology. 48(6): 955-961. [499]
8. Box, Thadis W.; White, Richard S. 1969. Fall and winter burning of south
Texas brush ranges. Journal of Range Management. 22(6): 373-376.
[11438]
9. Brown, David E.; Minnich, Richard A. 1986. Fire and changes in creosote
bush scrub of the western Sonoran Desert, California. American Midland
Naturalist. 116(2): 411-422. [537]
10. Burgess, Tony L.; Bowers, Janice E.; Turner, Raymond M. 1991. Exotic
plants at the Desert Laboratory, Tucson, Arizona. Madrono. 38(2):
96-114. [15362]
11. Everitt, J. H.; Gonzalez, C. L.; Scott, G.; Dahl, B. E. 1981. Seasonal
food preferences of cattle on native range in the south Texas plains.
Journal of Range Management. 34(5): 384-388. [12981]
12. Eyre, F. H., ed. 1980. Forest cover types of the United States and
Canada. Washington, DC: Society of American Foresters. 148 p. [905]
13. Garrison, George A.; Bjugstad, Ardell J.; Duncan, Don A.; [and others].
1977. Vegetation and environmental features of forest and range
ecosystems. Agric. Handb. 475. Washington, DC: U.S. Department of
Agriculture, Forest Service. 68 p. [998]
14. Gibbens, Robert P.; Herbel, Carlton H.; Lenz, James M. 1987. Field-scale
tebuthiuron application on brush-infested rangeland. Weed Technology. 1:
323-327. [4577]
15. Goldberg, Deborah E.; Turner, Raymond M. 1986. Vegetation change and
plant demography in permanent plots in the Sonoran Desert. Ecology.
67(3): 695-712. [4410]
16. Goodwin, John G., Jr.; Hungerford, C. Roger. 1977. Habitat use by native
Gambel's and scaled quail and released masked bobwhite quail in southern
Arizona. Res. Pap. RM-197. Fort Collins, CO: U.S. Department of
Agriculture, Forest Service, Rocky Mountain Forest and Range Experiment
Station. 8 p. [14970]
17. Hamilton, Wayne T. 1980. Suppressing undesirable plants in buffelgrass
range with prescribed fire. In: White, Larry D., ed. Prescribed range
burning in the Rio Grande Plains of Texas: Proceedings of a symposium;
1979 November 7; Carrizo Springs, TX. College Station, TX: The Texas A&M
University System, Texas Agricultural Extension Service: 12-21. [11459]
18. Hamilton, Wayne T. 1980. Prescribed burning of improved pastures. In:
Hanselka, C. Wayne, ed. Prescribed range burning in the coastal prairie
and eastern Rio Grande Plains of Texas: Proceedings of a symposium; 1980
October 16; Kingsville, TX. College Station, TX: The Texas A&M
University System, Texas Agricultural Extension Service: 114-128.
[11456]
19. Henrickson, James. 1974. Saline habitats and halophytic vegetation of
the Chihuahuan Desert region. In: Wauer, Roland H.; Riskind, David H.,
eds. Transactions of the symposium on the biological resources of the
Chihuahuan Desert region, United States and Mexico; 1974 October 17-18;
Alpine, TX. Transactions and Proceedings Series No. 3. Washington, DC:
U.S. Department of the Interior, National Park Service: 289-314.
[16063]
20. Henrickson, James; Johnston, Marshall C. 1986. Vegetation and community
types of the Chihuahuan Desert. In: Barlow, J. C.; [and others], eds.
Chihuahuan Desert--U.S. and Mexico, II. Alpine, TX: Sul Ross State
University: 20-39. [12979]
21. Humphrey, Robert R. 1974. Fire in the deserts and desert grassland of
North America. In: Kozlowski, T. T.; Ahlgren, C. E., eds. Fire and
ecosystems. New York: Academic Press: 365-400. [14064]
22. Jackson, Laura L.; McAuliffe, Joseph R.; Roundy, Bruce A. 1991. Desert
restoration. Restoration & Management Notes. 9(2): 71-79. [22746]
23. Kearney, Thomas H.; Peebles, Robert H.; Howell, John Thomas; McClintock,
Elizabeth. 1960. Arizona flora. 2d ed. Berkeley, CA: University of
California Press. 1085 p. [6563]
24. Kitchen, Lynn M.; Scifres, C. J.; Mutz, J. L. 1980. Susceptibility of
selected woody plants to pelleted picloram. Journal of Range Management.
33(5): 349-353. [10287]
25. Kuchler, A. W. 1964. Manual to accompany the map of potential vegetation
of the conterminous United States. Special Publication No. 36. New York:
American Geographical Society. 77 p. [1384]
26. Loftin, Samuel Robert. 1987. Postfire dynamics of a Sonoran Desert
ecosystem. Tempe, AZ: Arizona State University. 97 p. Thesis. [12296]
27. Lonard, Robert I.; Judd, Frank W. 1993. Phytogeography of the woody
flora of the lower Rio Grande Valley, Texas. Texas Journal of Science.
45(2): 133-147. [22040]
28. McLendon, Terry. 1991. Preliminary description of the vegetation of
south Texas exclusive of coastal saline zones. Texas Journal of Science.
43(1): 13-32. [14890]
29. Minckley, W. L.; Brown, David E. 1982. Wetlands. In: Brown, David E.,
ed. Biotic communities of the American Southwest--United States and
Mexico. Desert Plants. 4(1-4): 223-287. [8898]
30. Niering, William A.; Lowe, Charles H. 1984. Vegetation of the Santa
Catalina Mountains: community types and dynamics. Vegetatio. 58: 3-28.
[12037]
31. Powell, A. Michael. 1988. Trees & shrubs of Trans-Pecos Texas including
Big Bend and Guadalupe Mountains National Parks. Big Bend National Park,
TX: Big Bend Natural History Association. 536 p. [6130]
32. Raunkiaer, C. 1934. The life forms of plants and statistical plant
geography. Oxford: Clarendon Press. 632 p. [2843]
33. Rogers, Garry F.; Steele, Jeff. 1980. Sonoran Desert fire ecology. In:
Stokes, Marvin A.; Dieterich, John H., technical coordinators.
Proceedings of the fire history workshop; 1980 October 20-24; Tucson,
AZ. Gen. Tech. Rep. RM-81. Fort Collins, CO: U.S. Department of
Agriculture, Forest Service, Rocky Mountain Forest and Range Experiment
Station: 15-19. [16036]
34. Rudolf, Paul O. 1974. Lycium L. wolfberry. In: Schopmeyer, C. S., ed.
Seeds of woody plants in the United States. Agriculture Handbook No.
450. Washington, DC: U.S. Department of Agriculture, Forest Service:
522-524. [7699]
35. Shreve, Forrest; Hinckley, Arthur L. 1937. Thirty years of change in
desert vegetation. Ecology. 18(4): 463-478. [4574]
36. Stickney, Peter F. 1989. Seral origin of species originating in northern
Rocky Mountain forests. Unpublished draft on file at: U.S. Department of
Agriculture, Forest Service, Intermountain Research Station, Fire
Sciences Laboratory, Missoula, MT; RWU 4403 files. 7 p. [20090]
37. Turner, Raymond M.; Brown, David E. 1982. Sonoran desertscrub. In:
Brown, David E., ed. Biotic communities of the American
Southwest--United States and Mexico. Desert Plants. 4(1-4): 181-221.
[2375]
38. U.S. Department of Agriculture, Soil Conservation Service. 1982.
National list of scientific plant names. Vol. 1. List of plant names.
SCS-TP-159. Washington, DC. 416 p. [11573]
39. Van Dersal, William R. 1938. Native woody plants of the United States,
their erosion-control and wildlife values. Washington, DC: U.S.
Department of Agriculture. 362 p. [4240]
40. Varner, L. W.; Blankenship, L. H. 1987. Southern Texas shrubs--nutritive
value and utilization by herbivores. In: Provenza, Frederick D.;
Flinders, Jerran T.; McArthur, E. Durant, compilers.
Proceedings--symposium on plant-herbivore interactions; 1985 August 7-9;
Snowbird, UT. Gen. Tech. Rep. INT-222. Ogden, UT: U.S. Department of
Agriculture, Forest Service, Intermountain Research Station: 108-112.
[7404]
41. Vines, Robert A. 1960. Trees, shrubs, and woody vines of the Southwest.
Austin, TX: University of Texas Press. 1104 p. [7707]
42. Vora, Robin S. 1990. Plant phenology in the lower Rio Grande Valley,
Texas. Texas Journal of Science. 42(2): 137-142. [11832]
43. Vora, Robin S.; Messerly, John F. 1990. Changes in native vegetation
following different disturbances in the lower Rio Grande Valley, Texas.
Texas Journal of Science. 42(2): 151-158. [11831]
44. White, Richard S. 1969. Fire temperatures and the effect of burning on
south Texas brush communities. Lubbock, TX: Texas Technological College.
74 p. Thesis. [20741]
Index
Related categories for Species: Lycium berlandieri
| Berlandier Wolfberry
|
 |
