Natural Resources
Conservation Service
Ecological site R083AY016TX
Saline Clay Loam
Last updated: 9/19/2023
Accessed: 11/21/2024
General information
Provisional. A provisional ecological site description has undergone quality control and quality assurance review. It contains a working state and transition model and enough information to identify the ecological site.
Figure 1. Mapped extent
Areas shown in blue indicate the maximum mapped extent of this ecological site. Other ecological sites likely occur within the highlighted areas. It is also possible for this ecological site to occur outside of highlighted areas if detailed soil survey has not been completed or recently updated.
MLRA notes
Major Land Resource Area (MLRA): 083A–Northern Rio Grande Plain
This area is entirely in Texas and south of San Antonio. It makes up about 11,115 square miles (28,805 square kilometers). The towns of Uvalde, Cotulla, and Hondo are in the western part of the area, and Beeville, Goliad, and Kenedy are in the eastern part. The town of Alice is just outside the southern edge of the area. Interstate Highways 35 and 37 cross this area. This area is comprised of inland, dissected coastal plains.
Classification relationships
USDA-Natural Resources Conservation Service, 2006.
-Major Land Resource Area (MLRA) 83A
Ecological site concept
The Saline Clay Loam has clay loam surface textures coupled with salts. The presence of salts creates a unique plant community.
Associated sites
R083AY017TX |
Blackland |
---|---|
R083AY024TX |
Tight Sandy Loam |
R083AY027TX |
Western Clay Loam |
Similar sites
R083BY016TX |
Saline Clay Loam |
---|
Table 1. Dominant plant species
Tree |
(1) Prosopis glandulosa |
---|---|
Shrub |
(1) Ziziphus obtusifolia |
Herbaceous |
(1) Sporobolus airoides |
Physiographic features
These soils are on side slopes or shoulders of interfluves. Slopes range from 0 to 8 percent. This area is comprised of inland, dissected coastal plains.
Table 2. Representative physiographic features
Landforms |
(1)
Coastal plain
> Ridge
(2) Coastal plain > Interfluve |
---|---|
Runoff class | Medium to very high |
Elevation | 200 – 1,000 ft |
Slope | 8% |
Aspect | Aspect is not a significant factor |
Climatic features
MLRA 83A is subtropical, subhumid on the western boundary and subtropical humid on the eastern boundary. Winters are dry and mild and the summers are hot and humid. Tropical maritime air masses predominate throughout spring, summer, and fall. Modified polar air masses exert considerable influence during winter, creating a continental climate characterized by large variations in temperature. Average precipitation for MLRA 83A is 20 inches on the western boundary and 35 inches on the eastern boundary. Peak rainfall, because of rain showers, occurs late in spring and a secondary peak occurs early in fall. Heavy thunderstorm activities increase in April, May, and June. July is hot and dry with little weather variations. Rainfall increases again in late August and September as tropical disturbances increase and become more frequent. Tropical air masses from the Gulf of Mexico dominate during the spring, summer, and fall. Prevailing winds are southerly to southeasterly throughout the year except in December when winds are predominately northerly.
Table 3. Representative climatic features
Frost-free period (characteristic range) | 223-251 days |
---|---|
Freeze-free period (characteristic range) | 263-365 days |
Precipitation total (characteristic range) | 25-32 in |
Frost-free period (actual range) | 208-263 days |
Freeze-free period (actual range) | 254-365 days |
Precipitation total (actual range) | 24-37 in |
Frost-free period (average) | 235 days |
Freeze-free period (average) | 314 days |
Precipitation total (average) | 29 in |
Figure 2. Monthly precipitation range
Figure 3. Monthly minimum temperature range
Figure 4. Monthly maximum temperature range
Figure 5. Monthly average minimum and maximum temperature
Figure 6. Annual precipitation pattern
Figure 7. Annual average temperature pattern
Climate stations used
-
(1) CARRIZO SPRINGS 3W [USC00411486], Carrizo Springs, TX
-
(2) DILLEY [USC00412458], Dilley, TX
-
(3) FLORESVILLE [USC00413201], Floresville, TX
-
(4) KARNES CITY 2N [USC00414696], Karnes City, TX
-
(5) MATHIS 4 SSW [USC00415661], Mathis, TX
-
(6) PLEASANTON [USC00417111], Pleasanton, TX
-
(7) UVALDE 3 SW [USC00419268], Uvalde, TX
-
(8) BEEVILLE 5 NE [USC00410639], Beeville, TX
-
(9) CROSS [USC00412125], Tilden, TX
-
(10) GOLIAD [USC00413618], Goliad, TX
-
(11) LYTLE 3W [USC00415454], Natalia, TX
-
(12) TILDEN 4 SSE [USC00419031], Tilden, TX
-
(13) HONDO MUNI AP [USW00012962], Hondo, TX
-
(14) CHEAPSIDE [USC00411671], Gonzales, TX
-
(15) CUERO [USC00412173], Cuero, TX
-
(16) HONDO [USC00414254], Hondo, TX
-
(17) NIXON [USC00416368], Stockdale, TX
-
(18) CHARLOTTE 5 NNW [USC00411663], Charlotte, TX
-
(19) FOWLERTON [USC00413299], Fowlerton, TX
-
(20) PEARSALL [USC00416879], Pearsall, TX
-
(21) POTEET [USC00417215], Poteet, TX
-
(22) CALLIHAM [USC00411337], Calliham, TX
Influencing water features
Water features do not influence this site.
Wetland description
N/A
Soil features
The soils are deep to very deep, well drained, moderately slowly to very slowly permeable derived from calcareous clayey or loamy residuum weathered from sandstone and claystone. Soil series correlated to this site include: Campbellton and Schattel.
Table 4. Representative soil features
Parent material |
(1)
Residuum
–
shale
|
---|---|
Surface texture |
(1) Clay loam (2) Loam (3) Sandy clay loam (4) Clay |
Family particle size |
(1) Fine |
Drainage class | Moderately well drained to well drained |
Permeability class | Moderately slow to very slow |
Soil depth | 80 in |
Surface fragment cover <=3" | Not specified |
Surface fragment cover >3" | Not specified |
Available water capacity (0-40in) |
4 – 6 in |
Calcium carbonate equivalent (0-40in) |
25% |
Electrical conductivity (0-40in) |
16 mmhos/cm |
Sodium adsorption ratio (0-40in) |
12 |
Soil reaction (1:1 water) (0-40in) |
7.4 – 8.4 |
Subsurface fragment volume <=3" (Depth not specified) |
2% |
Subsurface fragment volume >3" (Depth not specified) |
1% |
Ecological dynamics
The Northern Rio Grande Plain MLRA was a disturbance-maintained system. Prior to European settlement (pre-1825), fire and grazing were the two primary forms of disturbance. Grazing by large herbivores included antelope, deer, and small herds of bison. The infrequent but intense, short-duration grazing by these species suppressed woody species and invigorated herbaceous species. The herbaceous savannah species adapted to fire and grazing disturbances by maintaining belowground tissues. Wright and Bailey (1982) report that there are no reliable records of fire frequency for the Rio Grande Plains because there are no trees to carry fire scars from which to estimate fire frequency. Because savannah grassland is typically of level or rolling topography, a natural fire frequency of three to seven years seems reasonable for this site.
Precipitation patterns are highly variable. Long-term droughts, occurring three to four times per century, cause shifts in species composition by causing die-off of seedlings, less drought-tolerant species, and some woody species. Droughts also reduce biomass production and create open space, which is colonized by opportunistic species when precipitation increases. Wet periods allow midgrasses to increase in dominance.
Historical accounts prior to 1800 identify grazing by herds of wild horses, followed by heavy grazing by sheep and cattle as settlement progressed. Grazing on early ranches changed natural graze-rest cycles to continuous grazing and stocking rates exceeded the carrying capacity. These shifts in grazing intensity and the removal of rest from the system reduced plant vigor for the most palatable species, which on this site were mid-grasses and palatable forbs. Shortgrasses and less palatable forbs began to dominate the site. This shift resulted in lower fuel loads, which reduced fire frequency and intensity. The reduction in fires resulted in an increase in size and density of woody species.
Today, primarily beef cattle graze rangeland and pastureland. However, horse numbers are increasing rapidly on small acreage properties in the region. There are some areas where dairy cattle, poultry, goats, and sheep are locally important. Whitetail deer, wild turkey, bobwhite quail, and dove are the major wildlife species, and hunting leases are a major source of income for many landowners in this area. Introduced pasture has been established on many acres of old cropland and in areas with deeper soils. Buffelgrass is the most common introduced plant on the site and to a lesser extent bermudagrass, guineagrass (Urochloa maxima), and kleingrass, which are more commonly used for hay. Cropland is found in the valleys, bottomlands, and deeper upland soils. Wheat (Triticum spp.), oats Avena spp.), forage and grain sorghum (Sorghum spp.), cotton (Gossypium spp.), and corn (Zea mays) are major crops in the region.
State and transition model
Figure 8. STM
More interactive model formats are also available.
View Interactive Models
More interactive model formats are also available.
View Interactive Models
Click on state and transition labels to scroll to the respective text
Ecosystem states
T1A | - | Absence of disturbance and natural regeneration over time, may coupled with excessive grazing pressure |
---|---|---|
T1B | - | Removal of vegetation followed by extensive soil disturbance and planting with non-native species |
R2A | - | Reintroduction of historic disturbance return intervals |
T2A | - | Removal of vegetation followed by extensive soil disturbance and planting with non-native species |
T3A | - | Absence of disturbance and natural regeneration over time, may coupled with excessive grazing pressure |
State 1 submodel, plant communities
State 2 submodel, plant communities
State 3 submodel, plant communities
State 1
Grassland
Dominant plant species
-
false Rhodes grass (Trichloris crinita), grass
-
alkali sacaton (Sporobolus airoides), grass
Community 1.1
Midgrass Dominant
The reference plant community is an open grassland dominated by midgrasses, including multi-flowered false Rhodesgrass, two-flowered trichloris, alkali sacaton, silver bluestem and Arizona cottontop. There are shortgrasses such as curly mesquite present, but in limited amounts. Perennial forbs including bushsunflower, orange zexmenia, and erect dayflower are common. Scattered individual and mottes of woody plants occurred, making up less than 10 percent of the total composition. These included blackbrush acacia, spiny hackberry, lotebush, and allthorn goatbush. An occasional honey mesquite dotted the landscape. The community is maintained by periodic fires (5 to 10 years), browsing, and grazing.
Figure 9. Annual production by plant type (representative values) or group (midpoint values)
Table 5. Annual production by plant type
Plant type | Low (lb/acre) |
Representative value (lb/acre) |
High (lb/acre) |
---|---|---|---|
Grass/Grasslike | 850 | 2400 | 3400 |
Shrub/Vine | 150 | 200 | 250 |
Forb | 100 | 150 | 200 |
Tree | 25 | 50 | 75 |
Total | 1125 | 2800 | 3925 |
Figure 10. Plant community growth curve (percent production by month). TX4800, Midgrass Dominant Community. Warm-season midgrasses with forbs and shrubs..
Jan | Feb | Mar | Apr | May | Jun | Jul | Aug | Sep | Oct | Nov | Dec |
---|---|---|---|---|---|---|---|---|---|---|---|
J | F | M | A | M | J | J | A | S | O | N | D |
1 | 1 | 2 | 10 | 20 | 20 | 5 | 8 | 15 | 10 | 6 | 2 |
Community 1.2
Short/Midgrass Dominant
This community is resilient, still under the influence of periodic fires, and can easily be transitioned back to community 1.1. This community is stable and maintainable. Continued heavy grazing, coupled with drought cycles, causes the dominant midgrasses to decrease in composition. The opening of the midgrass canopy has caused shortgrasses to increase, forbs to become more abundant, and woody seedlings are able to increase slightly. At this point in time, with reduction in stocking rates, periodic rest, and increased fire frequency, this community can be maintained or shifted back to the previous community. If overgrazing continues, midgrasses will continue to decline, fire frequency and intensity will decrease, and the community will continue to decline toward a totally altered state. Such species as multi-flowered false Rhodesgrass, Arizona cottontop and alkali sacaton are replaced by pink pappusgrass, hooded windmillgrass, plains lovegrass, and perennial three-awn. Shortgrasses like curly mesquite, Hall’s panicum, and sand dropseed also increase.
Figure 11. Annual production by plant type (representative values) or group (midpoint values)
Table 6. Annual production by plant type
Plant type | Low (lb/acre) |
Representative value (lb/acre) |
High (lb/acre) |
---|---|---|---|
Grass/Grasslike | 800 | 1900 | 3000 |
Shrub/Vine | 150 | 225 | 250 |
Forb | 100 | 175 | 250 |
Tree | 25 | 75 | 100 |
Total | 1075 | 2375 | 3600 |
Figure 12. Plant community growth curve (percent production by month). TX4803, Short/Midgrass Dominant Community, 10-15% woody canopy. Short and Midgrass Dominant with 10-15% woody canopy..
Jan | Feb | Mar | Apr | May | Jun | Jul | Aug | Sep | Oct | Nov | Dec |
---|---|---|---|---|---|---|---|---|---|---|---|
J | F | M | A | M | J | J | A | S | O | N | D |
1 | 1 | 2 | 10 | 20 | 20 | 5 | 8 | 15 | 10 | 6 | 2 |
Pathway 1.2A
Community 1.2 to 1.1
This community can be taken back to community 1.1 through the use of prescribed grazing and prescribed burning.
State 2
Shrubland
Dominant plant species
-
pink pappusgrass (Pappophorum bicolor), grass
-
Arizona cottontop (Digitaria californica), grass
Community 2.1
Mid/Shortgrass Shrubland Complex
Continued heavy grazing, no rest, greatly reduced fire frequency, and increasing shrub canopy cover have altered this community drastically. Midgrasses, though still present, are relegated to a position within the thorny shrubs. Water, energy, and mineral cycles are altered to some extent. Although rainfall still infiltrates within the shrub community, woody plants harvest the water, limiting the amount available for herbaceous production. In addition, light rainfall events are intercepted by woody canopies and stems and evaporate before reaching the soil surface. In this community, fire frequency and intensity are greatly reduced because of reduced fuel loads and litter accumulation. This state can be converted back to State 1 through the use of brush management, prescribed burning, and prescribed grazing. To do so requires significant energy input, outlays of capital, and relatively long periods of time. Because the shrub species are relatively resistant to most herbicides, mechanical methods of brush management are most often utilized. Rootplowing on this site should be avoided because this mechanism brings salt to the surface, increasing salinity in the surface horizons. Following brush management, periodic rest periods and appropriate stocking rates will be needed to restore the original plant community.
Figure 13. Annual production by plant type (representative values) or group (midpoint values)
Table 7. Annual production by plant type
Plant type | Low (lb/acre) |
Representative value (lb/acre) |
High (lb/acre) |
---|---|---|---|
Grass/Grasslike | 550 | 1300 | 2100 |
Shrub/Vine | 150 | 300 | 350 |
Forb | 75 | 200 | 300 |
Tree | 50 | 100 | 150 |
Total | 825 | 1900 | 2900 |
Figure 14. Plant community growth curve (percent production by month). TX4801, Mid/Shortgrasses Shrubland Community. Mid and shortgrasses with forbs and 20-50% woody canopy..
Jan | Feb | Mar | Apr | May | Jun | Jul | Aug | Sep | Oct | Nov | Dec |
---|---|---|---|---|---|---|---|---|---|---|---|
J | F | M | A | M | J | J | A | S | O | N | D |
1 | 1 | 2 | 10 | 20 | 20 | 5 | 8 | 15 | 10 | 6 | 2 |
Community 2.2
Wooded Grassland
The Wooded Grassland Community has woody canopies exceeding 40 percent. Midgrasses are found only within thorny shrubs and interspaces. Curly mesquite, Hall’s panicum, whorled dropseed may be the only species present. Fire on the site in this state is almost non-existent. This site can be brought back to state 2.1 but not without extensive input of energy and outlays of capital. Because of the diverse woody community, this site in this state is most often manipulated by roller-chopping to enhance it for white-tailed deer, northern bobwhite, or scaled quail. To further enhance it for wildlife, the woody plant community can be manipulated and grazed to maximize use for target species. Many landowners find managing towards this community for wildlife the most suitable option.
Figure 15. Annual production by plant type (representative values) or group (midpoint values)
Table 8. Annual production by plant type
Plant type | Low (lb/acre) |
Representative value (lb/acre) |
High (lb/acre) |
---|---|---|---|
Grass/Grasslike | 400 | 900 | 1300 |
Shrub/Vine | 150 | 350 | 400 |
Forb | 100 | 250 | 300 |
Tree | 50 | 150 | 200 |
Total | 700 | 1650 | 2200 |
Figure 16. Plant community growth curve (percent production by month). TX4804, Wooded Grassland Community, >40% canopy. Midgrasses are found only within thorny shrubs having woody canopies exceeding 40 percent and interspaces are dominated by shortgrasses..
Jan | Feb | Mar | Apr | May | Jun | Jul | Aug | Sep | Oct | Nov | Dec |
---|---|---|---|---|---|---|---|---|---|---|---|
J | F | M | A | M | J | J | A | S | O | N | D |
1 | 1 | 2 | 10 | 20 | 20 | 5 | 8 | 15 | 10 | 6 | 2 |
Pathway 2.2A
Community 2.2 to 2.1
Managerial activities that restore the hydrologic cycle, such as the energy captured by midgrasses, and restored ground cover will tend to move the Community 2.2 toward the Mid/Shortgrass Shrubland Complex (2.1). Selective brush management is needed to accomplish the desired canopy level and spatial arrangement of woody species. Integrated brush management and utilizing historic ecological disturbances such as herbivory and fire in are needed to maintain the desired brush densities. The time to shift back to the 10 to 40 percent canopy is dependent upon favorable growing conditions and could take three to five years.
Community 3.1
Introduced/Native Species
This community is a result of the land manager planting introduced or native grass species. Seeding with native species is uncommon due to the lack of availability of seeds that are adapted to saline soils of South Texas. Although this site is infrequently plowed due to salt and sodium content, mechanical manipulation has been done in some instances. When mechanical manipulation is done, the site is usually seeded to bell Rhodesgrass (Chloris gayana) or Kleberg bluestem. Either of these species, most commonly Kleberg bluestem, may invade this site when soils are denuded and native grasses are removed by overgrazing. Seeds of both Kleberg bluestem and bell Rhodesgrass are wind borne and a ready seed source is available from public roadways. Once the site is established to either of these species, return to a native state is extremely difficult, if not impossible.
Figure 17. Annual production by plant type (representative values) or group (midpoint values)
Table 9. Annual production by plant type
Plant type | Low (lb/acre) |
Representative value (lb/acre) |
High (lb/acre) |
---|---|---|---|
Grass/Grasslike | 700 | 1200 | 2100 |
Shrub/Vine | 50 | 100 | 150 |
Tree | 25 | 75 | 125 |
Forb | 25 | 75 | 125 |
Total | 800 | 1450 | 2500 |
Figure 18. Plant community growth curve (percent production by month). TX4762, Introduced Grass Community. Planted into introduced grasses for pasture planting..
Jan | Feb | Mar | Apr | May | Jun | Jul | Aug | Sep | Oct | Nov | Dec |
---|---|---|---|---|---|---|---|---|---|---|---|
J | F | M | A | M | J | J | A | S | O | N | D |
0 | 0 | 5 | 10 | 20 | 20 | 5 | 10 | 15 | 10 | 5 | 0 |
Transition T1A
State 1 to 2
The Grassland State will cross a threshold to Shrubland (State 2) with abusive grazing and without brush management or fire. Severe drought is also a significant factor. In State 2 more rainfall is being utilized by woody plants than the herbaceous plants. Because of the increased canopy, sunlight is being captured by the woody plants and converted to energy instead of the herbaceous plants.
Transition T1B
State 1 to 3
The transition to the Converted Land State is triggered by mechanical treatment and planting to native or introduced forages. Planting is usually done following brush management.
Restoration pathway R2A
State 2 to 1
Brush management is the key driver in restoring State 2 back to the Grassland State (1). Reduction in woody canopy below 20 percent will take large energy inputs depending on the canopy cover. A prescribed grazing plan and prescribed burning plan will keep the state functioning.
Transition T2A
State 2 to 3
The transition to the Seeded State is triggered by major ground disturbing mechanical treatment and planting to native or introduced forages. Planting is usually done following brush management.
Transition T3A
State 3 to 2
The transition from the Seeded State to the Shrubland State is triggered by neglect or no management over long periods of time. Shrubs re-establish from the seed bank and introduction from wildlife and livestock. A complete return to a previous state is not possible if adapted non-native plants have been established.
Additional community tables
Table 10. Community 1.1 plant community composition
Group | Common name | Symbol | Scientific name | Annual production (lb/acre) | Foliar cover (%) | |
---|---|---|---|---|---|---|
Grass/Grasslike
|
||||||
1 | Midgrasses | 400–1700 | ||||
alkali sacaton | SPAI | Sporobolus airoides | 100–500 | – | ||
multiflower false Rhodes grass | TRPL3 | Trichloris pluriflora | 100–450 | – | ||
large-spike bristlegrass | SEMA5 | Setaria macrostachya | 100–300 | – | ||
silver beardgrass | BOLAT | Bothriochloa laguroides ssp. torreyana | 100–300 | – | ||
false Rhodes grass | TRCR9 | Trichloris crinita | 50–250 | – | ||
Arizona cottontop | DICA8 | Digitaria californica | 50–150 | – | ||
2 | Grasses | 250–850 | ||||
pink pappusgrass | PABI2 | Pappophorum bicolor | 100–350 | – | ||
hooded windmill grass | CHCU2 | Chloris cucullata | 100–250 | – | ||
plains lovegrass | ERIN | Eragrostis intermedia | 100–250 | – | ||
lovegrass tridens | TRER | Tridens eragrostoides | 75–200 | – | ||
3 | Grasses | 100–450 | ||||
purple threeawn | ARPU9 | Aristida purpurea | 25–200 | – | ||
Texas bristlegrass | SETE6 | Setaria texana | 100–200 | – | ||
southwestern bristlegrass | SESC2 | Setaria scheelei | 50–150 | – | ||
Texas cottontop | DIPA6 | Digitaria patens | 25–100 | – | ||
slim tridens | TRMUM | Tridens muticus var. muticus | 25–100 | – | ||
4 | Shortgrasses | 100–400 | ||||
curly-mesquite | HIBE | Hilaria belangeri | 50–150 | – | ||
Hall's panicgrass | PAHA | Panicum hallii | 20–100 | – | ||
sand dropseed | SPCR | Sporobolus cryptandrus | 50–100 | – | ||
buffalograss | BODA2 | Bouteloua dactyloides | 20–50 | – | ||
fall witchgrass | DICO6 | Digitaria cognata | 5–50 | – | ||
Madagascar dropseed | SPPY2 | Sporobolus pyramidatus | 10–20 | – | ||
knot grass | SEREF | Setaria reverchonii ssp. firmula | 5–10 | – | ||
Texas grama | BORI | Bouteloua rigidiseta | 0–5 | – | ||
red grama | BOTR2 | Bouteloua trifida | 0–5 | – | ||
Forb
|
||||||
5 | Forbs | 50–100 | ||||
awnless bushsunflower | SICA7 | Simsia calva | 25–50 | – | ||
whitemouth dayflower | COER | Commelina erecta | 10–20 | – | ||
Gregg's tube tongue | JUPI5 | Justicia pilosella | 5–20 | – | ||
6 | Forbs | 25–50 | ||||
littleleaf sensitive-briar | MIMI22 | Mimosa microphylla | 20–40 | – | ||
prairie clover | DALEA | Dalea | 10–30 | – | ||
globemallow | SPHAE | Sphaeralcea | 5–20 | – | ||
7 | Forbs | 25–50 | ||||
Cuman ragweed | AMPS | Ambrosia psilostachya | 10–50 | – | ||
fanpetals | SIDA | Sida | 10–30 | – | ||
Forb, perennial | 2FP | Forb, perennial | 5–20 | – | ||
Rio Grande stickpea | CACO | Calliandra conferta | 5–15 | – | ||
broom snakeweed | GUSA2 | Gutierrezia sarothrae | 0–15 | – | ||
Drummond's goldenbush | ISDR | Isocoma drummondii | 0–15 | – | ||
weakleaf bur ragweed | AMCO3 | Ambrosia confertiflora | 5–10 | – | ||
silverleaf nightshade | SOEL | Solanum elaeagnifolium | 0–10 | – | ||
bristleleaf pricklyleaf | THTE7 | Thymophylla tenuiloba | 5–10 | – | ||
Forb, annual | 2FA | Forb, annual | 1–5 | – | ||
cheeseweed mallow | MAPA5 | Malva parviflora | 1–5 | – | ||
smartweed leaf-flower | PHPO3 | Phyllanthus polygonoides | 1–5 | – | ||
desert goosefoot | CHPR5 | Chenopodium pratericola | 1–5 | – | ||
Texas bindweed | COEQ | Convolvulus equitans | 1–5 | – | ||
Shrub/Vine
|
||||||
8 | Shrubs/Vines | 150–250 | ||||
lotebush | ZIOB | Ziziphus obtusifolia | 20–70 | – | ||
Brazilian bluewood | COHO | Condalia hookeri | 10–50 | – | ||
blackbrush acacia | ACRI | Acacia rigidula | 10–50 | – | ||
spiny hackberry | CEEH | Celtis ehrenbergiana | 20–50 | – | ||
fourwing saltbush | ATCA2 | Atriplex canescens | 10–20 | – | ||
catclaw acacia | ACGRG3 | Acacia greggii var. greggii | 10–20 | – | ||
pricklypear | OPUNT | Opuntia | 10–20 | – | ||
desert yaupon | SCCU4 | Schaefferia cuneifolia | 5–10 | – | ||
lime pricklyash | ZAFA | Zanthoxylum fagara | 5–10 | – | ||
Texas lignum-vitae | GUAN | Guaiacum angustifolium | 5–10 | – | ||
clapweed | EPAN | Ephedra antisyphilitica | 5–10 | – | ||
Schaffner's wattle | ACSCB | Acacia schaffneri var. bravoensis | 5–10 | – | ||
whitebrush | ALGR2 | Aloysia gratissima | 5–10 | – | ||
Texan goatbush | CAERT | Castela erecta ssp. texana | 5–10 | – | ||
Christmas cactus | CYLE8 | Cylindropuntia leptocaulis | 1–10 | – | ||
javelina bush | COER5 | Condalia ericoides | 1–5 | – | ||
catclaw acacia | ACGRW | Acacia greggii var. wrightii | 2–5 | – | ||
Shrub, other | 2S | Shrub, other | 1–5 | – | ||
leatherstem | JADI | Jatropha dioica | 0–5 | – | ||
crown of thorns | KOSP | Koeberlinia spinosa | 1–5 | – | ||
Berlandier's wolfberry | LYBE | Lycium berlandieri | 1–5 | – | ||
Texas paloverde | PATE10 | Parkinsonia texana | 1–5 | – | ||
Tree
|
||||||
9 | Trees | 25–75 | ||||
honey mesquite | PRGL2 | Prosopis glandulosa | 25–75 | – |
Interpretations
Animal community
As a historic tall/midgrass prairie, this site was occupied by bison, antelope, deer, quail, turkey, and dove. This site was also used by many species of grassland songbirds, migratory waterfowl, and coyotes. This site now provides forage for livestock and is still used by quail, dove, migratory waterfowl, grassland birds, coyotes, and deer.
Feral hogs (Sus scrofa) can be found on most ecological sites in Texas. Damage caused by feral hogs each year includes, crop damage by rutting up crops, destroyed fences, livestock watering areas, and predation on native wildlife, and ground-nesting birds. Feral hogs have few natural predators, thus allowing their population to grow to high numbers.
Wildlife habitat is a complex of many different plant communities and ecological sites across the landscape. Most animals use the landscape differently to find food, shelter, protection, and mates. Working on a conservation plan for the whole property, with a local professional, will help managers make the decisions that allow them to realize their goals for wildlife and livestock.
Grassland State (1): This state provides the maximum amount of forage for livestock such as cattle. It is also utilized by deer, quail and other birds as a source of food. When a site is in the reference plant community phase (1.1) it will also be used by some birds for nesting, if other habitat requirements like thermal and escape cover are near.
Tree/Shrubland Complex (2): This state can be maintained to meet the habitat requirements of cattle and wildlife. Land managers can find a balance that meets their goals and allows them flexibility to manage for livestock and wildlife. Forbs for deer and birds like quail will be more plentiful in this state. There will also be more trees and shrubs to provide thermal and escape cover for birds as well as cover for deer.
Converted Land State (3): The quality of wildlife habitat this site will produce is extremely variable and is influenced greatly by the timing of rain events. This state is often manipulated to meet landowner goals. If livestock production is the main goal, it can be converted to pastureland. It can also be planted to a mix of grasses and forbs that will benefit both livestock and wildlife. A mix of forbs in the pasture could attract pollinators, birds and other types of wildlife. Food plots can also be planted to provide extra nutrition for deer.
This rating system provides general guidance as to animal preference for plant species. It also indicates possible competition between kinds of herbivores for various plants. Grazing preference changes from time to time, especially between seasons, and between animal kinds and classes. Grazing preference does not necessarily reflect the ecological status of the plant within the plant community. For wildlife, plant preferences for food and plant suitability for cover are rated. Refer to habitat guides for a more complete description of a species habitat needs.
Hydrological functions
The grassland and the shrubland communities on this site use all the water from rainfall events that occur. Research has shown that the evapotranspiration rate on the grassland and the shrubland is nearly the same. Very little water could be harvested from this site if the woody plant community is replaced by a grass dominated community.
Recreational uses
White-tailed deer, quail, javelina, and feral hogs are hunted on the site. Bird watching may also be done.
Supporting information
Inventory data references
Information presented was derived from the revised Range Site, literature, limited NRCS clipping data (417s), field observations, and personal contacts with range-trained personnel.
Other references
AgriLife. 2009. Managing Feral Hogs Not a One-shot Endeavor. AgNews, April 23, 2009. http://agnews.tamu.edu/showstory.php?id=903.
Archer, S. 1995. Herbivore mediation of grass-woody plant interactions. Tropical Grasslands, 29:218-235.
Archer, S. 1995. Tree-grass dynamics in a Prosopis-thornscrub savanna parkland: reconstructing the past and predicting the future. Ecoscience, 2:83-99.
Archer, S. 1994. Woody plant encroachment into southwestern grasslands and savannas: rates, patterns and proximate causes. Ecological implications of livestock herbivory in the West, 13-68.
Archer, S. and F. E. Smeins. 1991. Ecosystem-level Processes. In Grazing Management: An Ecological Perspective. Edited by R.K. Heischmidt and J.W. Stuth. Timber Press, Portland, OR.
Baen, J. S. 1997. The growing importance and value implications of recreational hunting leases to agricultural land investors. Journal of Real Estate Research, 14:399-414.
Bailey, V. 1905. North American Fauna No. 25: Biological Survey of Texas. United States Department of Agriculture Biological Survey. Government Printing Office, Washington D. C.
Bestelmeyer, B. T., J.R. Brown, K. M. Havstad, R. Alexander, G. Chavez, and J. E. Herrick. 2003. Development and use of state-and-transition models for rangelands. Journal of Range Management, 56(2):114-126.
Box, T. W. 1960. Herbage production on four range plant communities in South Texas. Journal of Range Management, 13:72-76.
Briske, B B, B. T. Bestelmeyer, T. K. Stringham, and P. L. Shaver. 2008. Recommendations for development of resilience-based State-and-Transition Models. Rangeland Ecology and Management, 61:359-367.
Brown, J. R. and S. Archer. 1999. Shrub invasion of grassland: recruitment is continuous and not regulated by herbaceous biomass or density. Ecology, 80(7):2385-2396.
Diamond, D. D. and T. E. Fulbright. 1990. Contemporary plant communities of upland grasslands of the Coastal Sand Plain, Texas. Southwestern Naturalist, 35:385-392.
Dillehay T. 1974. Late quaternary bison population changes on the Southern Plains. Plains Anthropologist, 19:180-96.
Edward, D. B. 1836. The history of Texas; or, the immigrants, farmers, and politicians guide to the character, climate, soil and production of that country. Geographically arranged from personal observation and experience. J. A. James and Co., Cincinnati, OH.
Everitt, J. H., D. L. Drawe, and R. I. Leonard. 2002. Trees, Shrubs, and Cacti of South Texas. Texas Tech University Press, Lubbock, TX.
Everitt, J. H., D. L. Drawe, and R. I. Lonard. 1999. Field Guide to the Broad-Leaved Herbaceous Plants of South Texas. Texas Tech University Press. Lubbock, TX.
Foster, J. H. 1917. Pre-settlement fire frequency regions of the United States: a first approximation. Tall Timbers Fire Ecology Conference Proceedings No. 20.
Foster, W. C., ed. 1998. The La Salle Expedition to Texas: The Journal of Henry Joutel, 1684-1687. Texas State Historical Association, Austin, TX.
Frost, C. C. 1995. Presettlement fire regimes in southeastern marshes, peatlands, and swamps. In: Prodeedings, 19th Tall Timbers fire ecology conference, 39-60. Tall Timbers Research Station, Tallahassee, FL.
Fulbright, T. E. and S. L. Beasom. 1987. Long-term effects of mechanical treatment on white-tailed deer browse. Wildlife Society Bulletin, 15:560-564.
Fulbright, T. E., J. A. Ortega-Santos, A. Lozano-Cavazos, and L. E. Ramirez-Yanez. 2006. Establishing vegetation on migrating inland sand dunes in Texas. Rangeland Ecology and Management, 59:549-556.
Fulbright, T. E., D. D. Diamond, J. Rappole, and J. Norwine. The Coastal Sand Plain of Southern Texas. Rangelands, 12:337-340.
Gould, F. W. 1975. The Grasses of Texas. Texas A&M University Press, College Station, TX.
Grace, J. B., L. K. Allain, H. Q. Baldwin, A. G. Billock, W. R. Eddleman, A. M. Given, C. W. Jeske, and R. Moss. 2005. Effects of prescribed fire in the coastal prairies of Texas. USGS Open File Report 2005-1287.
Hamilton, W. and D. Ueckert. 2005. Rangeland Woody Plant Control: Past, Present, and Future. In: Brush Management: Past, Present, and Future, 3-16. Texas A&M University Press. College Station, TX.
Hansmire, J. A., D. L. Drawe, B. B. Wester and C.M. Britton. 1988. Effect of winter burns on forbs and grasses of the Texas Coastal Prairie. The Southwestern Naturalist, 33(3):333-338.
Heitschmidt R. K., Stuth J. W., eds. 1991. Grazing management: an ecological perspective. Timberline Press, Portland, OR.
Inglis, J. M. 1964. A history of vegetation of the Rio Grande Plains. Texas Parks and Wildlife Department Bulletin No. 45, Austin, TX.
Kneuper, C. L., C. B. Scott, and W. E. Pinchak. 2003. Consumption and dispersion of mesquite seeds by ruminants. Journal of Range Management, 56:255-259.
Kramp, B., R. Ansley, and D. Jones. 1998. Effect of prescribed fire on mesquite seedlings. Texas Tech University Research Highlights - Range, Wildlife and Fisheries Management, 29:13.
Le Houerou, H. N. and J. Norwine. 1988. The ecoclimatology of South Texas. In Arid lands: today and tomorrow. Edited by E. E. Whitehead, C. F. Hutchinson, B. N. Timmesman, and R. G. Varady, 417-444. Westview Press, Boulder, CO.
Lehman, V. W. 1965. Fire in the range of Attwater’s prairie chicken. Tall Timbers Fire Ecology Conference, 4:127-143.
Lehman, V. W. 1969. Forgotten Legions: Sheep in the Rio Grande Plain of Texas. Texas Western Press, El Paso, TX.
Mann, C. 2004. 1491. New Revelations of the Americas before Columbus. Vintage Books, New York City, NY.
Mapston, M. E. 2009. Feral Hogs in Texas. Rep. Texas Cooperative Extension. 23 Apr. 2009 http://icwdm.org/Publications/pdf/Feral%20Pig/Txferalhogs.pdf
McClendon, T. 1991. Preliminary description of the vegetation of South Texas exclusive of the Coastal Saline Zones. Texas Journal of Science, 43:13-32.
McGinty A., D. N. Ueckert. 2001. The Brush Busters success story. Rangelands, 23:3-8.
McLendon, T. 1991. Preliminary description of the vegetation of south Texas exclusive of coastal saline zones. Texas Journal of Science, 43:13-32.
Norwine, J. 1978. Twentieth-century semiarid climates and climatic fluctuations in Texas and northeastern Mexico. Journal of Arid Environments, 1:313-325.
Norwine, J. and R. Bingham. 1986. Frequency and severity of droughts in South Texas: 1900-1983, 1-17. In Livestock and wildlife management during drought. Edited by R. D. Brown. Caesar Kleberg Wildlife Research Institute, Kingsville, TX.
Olmsted, F. L. 1857. A journey through Texas, or a saddle trip on the Southwest frontier: with a statistical appendix. Dix, Edwards, and co., New York, London.
Prichard, D. 1998. A User Guide to Assessing Proper Functioning Condition and the Supporting Science for Lentic Areas. Bureau of Land Management. National Applied Resource Sciences Center, CO.
Rappole, J. H. and G. W. Blacklock. 1994. A field guide: Birds of Texas. Texas A&M University Press, College Station, TX.
Rhyne, M. Z. 1998. Optimization of wildlife and recreation earnings for private landowners. M. S. Thesis, Texas A&M University-Kingsville, Kingsville, TX.
Schindler, J. R. and T. E. Fulbright. 2003. Roller chopping effects on Tamaulipan scrub community composition. Journal of Range Management, 56:585-590.
Schmidley, D. J. 1983. Texas mammals east of the Balcones Fault zone. Texas A&M University Press, College Station, TX.
Scifres C. J., W. T. Hamilton, J. R. Conner, J. M. Inglis, and G. A. Rasmussen. 1985. Integrated Brush Management Systems for South Texas: Development and Implementation. Texas Agricultural Experiment Station, College Station, TX.
Scifres, C. J. and W. T. Hamilton. 1993. Prescribed burning for brushland management: the South Texas example. Texas A&M Press, College Station, TX.
Scifres, C. J. 1975. Systems for improving McCartney rose infested coastal prairie rangeland. Texas Agricultural Experiment Station Bulletin MP 1225.
Smeins, F. E., S. Fuhlendorf, and C. Taylor, Jr. 1997. Environmental and Land Use Changes: A Long Term Perspective. In Juniper Symposium, 1-21. Texas Agricultural Experiment Station.
Smeins, F. E., D. D. Diamond, and W. Hanselka. 1991. Coastal prairie, 269-290. In Ecosystems of the World: Natural Grasslands. Edited by R. T. Coupland. Elsevier Press, Amsterdam, Netherlands.
Soil Survey Staff, Natural Resources Conservation Service, United States Department of Agriculture. Soil Survey Geographic (SSURGO) Database.
Snyder, R. A. and C. L. Boss. 2002. Recovery and stability in barrier island plant communities. Journal of Coastal Research, 18:530-536.
Stiles, H. R., ed. 1906. Joutel’s journal of La Salle’s last voyage, 1686-1687. Joseph McDonough, Albany, NY.
Stringham, T. K., W. C. Krueger, and P. L. Shaver. 2001. State and transition modeling: and ecological process approach. Journal of Range Management, 56(2):106-113.
Texas A&M Research and Extension Center. 2000. Native Plants of South Texas http://uvalde.tamu.edu/herbarium/index.html.
Texas Agriculture Experiment Station. 2007. Benny Simpson’s Texas Native Trees http://aggie-horticulture.tamu.edu/ornamentals/natives/.
Texas Parks and Wildlife Department. 2007. List of White-tailed Deer Browse and Ratings. District 8.
Tharp, B. C. 1926. Structure of Texas Vegetation east of the 98th meridian. Bulletin 2606. University of Texas, Austin. TX.
Thurow, T. L. 1991. Hydrology and Erosion. In: Grazing Management: An Ecological Perspective. Edited by R.K. Heitschmidt and J.W. Stuth. Timber Press, Portland, OR.
Urbatsch, L. 2000. Chinese tallow tree (Triadica sebifera (L.) Small. USDA-NRCS Plant Guide.
USDA-NRCS Plant Database. 2018. https://plants.usda.gov/.
Van’t Hul, J. T., R. S. Lutz and N. E. Mathews. 1997. Impact of prescribed burning on vegetation and bird abundance on Matagorda Island, Texas. Journal of Range Management, 50:346-360.
Vines, R. A. 1984. Trees of Central Texas. University of Texas Press, Austin, TX.
Wade, D. D., B. L. Brock, P. H. Brose, J. B. Grace, G. A. Hoch, and W. A. Patterson III. 2000. Fire in Eastern ecosystems. In Wildland fire in ecosystems: effects of fire on flora. Edited by. J. K. Brown and J. Kaplers. United States Forest Service, Rocky Mountain Research Station, Ogden, UT.
Weltz, M. A. and W. H. Blackburn. 1995. Water budget for south Texas rangelands. Journal of Range Management, 48:45-52.
Whittaker, R. H., L. E. Gilbert, and J. H. Connell. 1979. Analysis of a two-phase pattern in a mesquite grassland, Texas. Journal of Ecology, 67:935-52.
Wright, B. D., R. K. Lyons, J. C. Cathey, and S. Cooper. 2002. White-tailed deer browse preferences for South Texas and the Edwards Plateau. Texas Cooperative Extension Bulletin B-6130.
Wright, H.A. and A.W. Bailey. 1982. Fire Ecology: United States and Southern Canada. John Wiley & Sons, Inc., Hoboken, NJ.
Approval
Bryan Christensen, 9/19/2023
Acknowledgments
Reviewers:
Vivian Garcia, RMS, NRCS, Corpus Christi, Texas
Shanna Dunn, RSS, NRCS, Corpus Christi, Texas
Justin Clary, RMS, NRCS, Temple, Texas
Rangeland health reference sheet
Interpreting Indicators of Rangeland Health is a qualitative assessment protocol used to determine ecosystem condition based on benchmark characteristics described in the Reference Sheet. A suite of 17 (or more) indicators are typically considered in an assessment. The ecological site(s) representative of an assessment location must be known prior to applying the protocol and must be verified based on soils and climate. Current plant community cannot be used to identify the ecological site.
Author(s)/participant(s) | Vivian Garcia, RMS, NRCS, Corpus Christi, Texas |
---|---|
Contact for lead author | 361-241-0609 |
Date | 03/01/2008 |
Approved by | Bryan Christensen |
Approval date | |
Composition (Indicators 10 and 12) based on | Annual Production |
Indicators
-
Number and extent of rills:
None. -
Presence of water flow patterns:
Somewhat, because of location on toe slopes of hills and ridges. -
Number and height of erosional pedestals or terracettes:
None. -
Bare ground from Ecological Site Description or other studies (rock, litter, lichen, moss, plant canopy are not bare ground):
0 to 5 percent bare ground. Small and non-connected areas. -
Number of gullies and erosion associated with gullies:
None. -
Extent of wind scoured, blowouts and/or depositional areas:
None. -
Amount of litter movement (describe size and distance expected to travel):
Minimal and short. -
Soil surface (top few mm) resistance to erosion (stability values are averages - most sites will show a range of values):
-
Soil surface structure and SOM content (include type of structure and A-horizon color and thickness):
Depth is from 4 to 12 inches, dark grayish brown (10YR 4/2) clay loam or sandy clay loam; moderate fine subangular blocky structure; hard and friable; neutral to mildly alkaline; many fine and medium roots; few fine tubular pores; noncalcareous; SOM is 0 to 3 percent. -
Effect of community phase composition (relative proportion of different functional groups) and spatial distribution on infiltration and runoff:
High canopy, basal cover and density with small interspaces should make rainfall impact negligible. This site has well drained soils, deep with 0 to 3 percent slopes which allows negligible runoff and erosion. -
Presence and thickness of compaction layer (usually none; describe soil profile features which may be mistaken for compaction on this site):
None. -
Functional/Structural Groups (list in order of descending dominance by above-ground annual-production or live foliar cover using symbols: >>, >, = to indicate much greater than, greater than, and equal to):
Dominant:
Warm-season midgrasses >>Sub-dominant:
Warm-season shortgrasses >Other:
Forbs > Shrubs/Vines > TreesAdditional:
Forbs make up to five percent of species composition, shrubs and trees compose five percent species composition. -
Amount of plant mortality and decadence (include which functional groups are expected to show mortality or decadence):
Grasses, due to their growth habit, will exhibit some mortality and decadence, though very slight. -
Average percent litter cover (%) and depth ( in):
Litter is primarily herbaceous. -
Expected annual annual-production (this is TOTAL above-ground annual-production, not just forage annual-production):
2,250 to 3,750 pounds per acre. -
Potential invasive (including noxious) species (native and non-native). List species which BOTH characterize degraded states and have the potential to become a dominant or co-dominant species on the ecological site if their future establishment and growth is not actively controlled by management interventions. Species that become dominant for only one to several years (e.g., short-term response to drought or wildfire) are not invasive plants. Note that unlike other indicators, we are describing what is NOT expected in the reference state for the ecological site:
Woody increasers that invade include blackbrush acacia, lotebush, allthorn goatbush, whitebrush, and prickly pear. Drummond's goldenweed may invade this site heavily. Introduced grasses that may invade include Kleberg bluestem. -
Perennial plant reproductive capability:
All species should be capable of plant reproduction, except during periods of prolonged drought, heavy natural herbivory, and/or wild fires.
Print Options
Sections
Font
Other
The Ecosystem Dynamics Interpretive Tool is an information system framework developed by the USDA-ARS Jornada Experimental Range, USDA Natural Resources Conservation Service, and New Mexico State University.
Click on box and path labels to scroll to the respective text.
Ecosystem states
T1A | - | Absence of disturbance and natural regeneration over time, may coupled with excessive grazing pressure |
---|---|---|
T1B | - | Removal of vegetation followed by extensive soil disturbance and planting with non-native species |
R2A | - | Reintroduction of historic disturbance return intervals |
T2A | - | Removal of vegetation followed by extensive soil disturbance and planting with non-native species |
T3A | - | Absence of disturbance and natural regeneration over time, may coupled with excessive grazing pressure |