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Ecological site R150AY526TX

Southern Blackland

Last updated: 9/22/2023
Accessed: 11/21/2024

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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.

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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): 150A–Gulf Coast Prairies

MLRA 150A is in the West Gulf Coastal Plain Section of the Coastal Plain Province of the Atlantic Plain in Texas (83 percent) and Louisiana (17 percent). It makes up about 16,365 square miles (42,410 square kilometers). It is characterized by nearly level plains that have low local relief and are dissected by rivers and streams that flow toward the Gulf of Mexico. Elevation ranges from sea level to about 165 feet (0 to 50 meters) along the interior margin. It includes the towns of Crowley, Eunice, and Lake Charles, Louisiana, and Beaumont, Houston, Bay City, Victoria, Corpus Christi, Robstown, and Kingsville, Texas. Interstates 10 and 45 are in the northeastern part of the area, and Interstate 37 is in the southwestern part. U.S. Highways 90 and 190 are in the eastern part, in Louisiana. U.S. Highway 77 passes through Kingsville, Texas. The Attwater Prairie Chicken National Wildlife Refuge and the Fannin Battleground State Historic Site are in the part of the area in Texas.

Classification relationships

USDA-Natural Resources Conservation Service, 2006.
-Major Land Resource Area (MLRA) 150A

Ecological site concept

The Southern Blackland ecological site shows an intact grass community with small clumped dispersal of woody species. The soils are very deep, richly black in color, and characterized by their shrink-swell nature. The sites are widely distributed across the uplands and terraces in areas with mean annual precipitation ranging from 32 to 41 inches.

Associated sites

R150AY639TX	Clay Loam The Clay Loam ecological site has very deep clay loam soils and has high vegetative production.
R150AY527TX	Clayey Bottomland The Clayey Bottomland site has very deep, clayey surface textured soils that occur on flood plains. The areas can be flooded and ponded for lengthy durations throughout the year.
R150AY528TX	Claypan Prairie The Claypan Prairie is a grassland site that occurs on nearly level, lower lying areas. Drainage in this site varies. The soils are characterized by a thin layer of fine sandy loam topsoil underlain by deep clay and clay loam subsoils. This site is slightly lower and down-slope of the Blackland site.
R150AY535TX	Southern Loamy Prairie The Southern Loamy Prairie is characterized by very deep loamy soils occurring on uplands. They are vegetatively productive and provide good grazing for livestock. This site is in adjacent areas.
R150AY537TX	Lowland As named, the Lowland ecological site occurs on the lowest part of the landscape. It receives excess water from surround landforms and may stay wet for extended periods throughout the year. This site is located within the Blackland site.
R150AY641TX	Lakebed Lakebeds are shallow depressions that support wet soil plant communities. These sites receive water from surrounding upland sites following heavy rainfall events and can remain ponded for long periods.

Similar sites

R150AY740TX	Northern Blackland The Northern Blackland ecological site shows an intact grass community with small clumped dispersal of woody species. The soils are very deep, richly black in color, and characterized by their shrink-swell nature. The sites are widely distributed across the uplands and terraces throughout the region. The site is correlated to areas with mean annual rainfall that ranges from 48 to 57 inches.

R150AY740TX

Northern Blackland

The Northern Blackland ecological site shows an intact grass community with small clumped dispersal of woody species. The soils are very deep, richly black in color, and characterized by their shrink-swell nature. The sites are widely distributed across the uplands and terraces throughout the region. The site is correlated to areas with mean annual rainfall that ranges from 48 to 57 inches.

Table 1. Dominant plant species

Tree	Not specified
Shrub	Not specified
Herbaceous	(1) Schizachyrium scoparium (2) Sorghastrum nutans

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Physiographic features

The Southern Blackland site in MRLA 150A was formed by clayey fluviodeltaic sediments in the Beaumont Formation of Late Pleistocene age. These nearly level to very gently sloping soils are on the South Texas coastal plain. Slopes are mainly less than 1 percent but can range as high as 8 percent. Runoff is medium on 0 to 1 percent, high on 1 to 3 percent, and very high on slopes greater than 3 percent. Undisturbed areas exhibit gilgai microrelief. Elevation ranges from 15 to 230 feet.

Table 2. Representative physiographic features

Landforms	(1) Coastal plain > Flat > Gilgai
Runoff class	Medium to very high
Flooding frequency	None
Ponding frequency	None
Elevation	15 – 230 ft
Slope	8%
Water table depth	60 – 80 in
Aspect	Aspect is not a significant factor

Climatic features

The climate of MLRA 150A is humid subtropical with mild winters. The average annual precipitation in the northern two-thirds of this area is 45 to 63 inches. It is 28 inches at the extreme southern tip of the area and 30 to 45 inches in the southwestern third of the area. The precipitation is fairly evenly distributed, but it is slightly higher in late summer and midsummer in the western part of the area and slightly higher in winter in the eastern part. Rainfall typically occurs as moderate intensity, tropical storms that produce large amounts of rain during the winter. The average annual temperature is 66 to 72 degrees F. The freeze-free period averages 325 days and ranges from 290 to 365 days, increasing in length to the southwest.

Table 3. Representative climatic features

Frost-free period (characteristic range)	252-283 days
Freeze-free period (characteristic range)	365 days
Precipitation total (characteristic range)	32-41 in
Frost-free period (actual range)	235-365 days
Freeze-free period (actual range)	365 days
Precipitation total (actual range)	31-42 in
Frost-free period (average)	279 days
Freeze-free period (average)	365 days
Precipitation total (average)	36 in

Characteristic range

Actual range

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Figure 2. Monthly precipitation range

Characteristic range

Actual range

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Figure 3. Monthly minimum temperature range

Characteristic range

Actual range

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Figure 4. Monthly maximum temperature range

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Figure 5. Monthly average minimum and maximum temperature

Figure 6. Annual precipitation pattern

Figure 7. Annual average temperature pattern

Climate stations used

(1) BEEVILLE CHASE NAAS [USW00012925], Beeville, TX
(2) CORPUS CHRISTI [USW00012924], Corpus Christi, TX
(3) KINGSVILLE NAAS [USW00012928], Kingsville, TX
(4) POINT COMFORT [USC00417140], Port Lavaca, TX
(5) REFUGIO 2 NW [USC00417533], Refugio, TX
(6) REFUGIO 3 SW [USC00417530], Refugio, TX
(7) ROBSTOWN [USC00417677], Robstown, TX
(8) SINTON [USC00418354], Sinton, TX
(9) VICTORIA FIRE DEPT #5 [USC00419361], Victoria, TX
(10) VICTORIA RGNL AP [USW00012912], Victoria, TX
(11) VICTORIA RGNL AP [USC00419367], Victoria, TX
(12) WELDER WILDLIFE FNDN [USC00419559], Sinton, TX
(13) BISHOP [USC00410805], Bishop, TX
(14) C C BOTANICAL GARDENS [USC00412013], Corpus Christi, TX
(15) PORT LAVACA [USC00417183], Port Lavaca, TX

Influencing water features

Water enters the soil rapidly when it is dry and cracked, and very slowly when it is wet and sealed. The site does not have a water table near the surface. No ponding or flooding is expected for this site.

Wetland description

This site has non-hydric soils. A few sites may have small areas of hydric soils that are mostly water holding depressions. Onsite investigation is necessary to determine exact local conditions.

Soil features

Southern Blackland consist of very deep, moderately well to well drained, very slowly permeable, slightly acid to moderately alkaline soils. The surface color is black to very dark gray. Soils correlated to this site include: Banquete, Contee, Dacosta, Laewest, and Victoria series.

Table 4. Representative soil features

Parent material	(1) Fluviomarine deposits – igneous, metamorphic and sedimentary rock
Surface texture	(1) Clay (2) Sandy clay loam (3) Clay loam
Family particle size	(1) Fine
Drainage class	Moderately well drained to well drained
Permeability class	Slow to very slow
Soil depth	80 in
Surface fragment cover <=3"	Not specified
Surface fragment cover >3"	Not specified
Available water capacity (0-60in)	7 – 11 in
Calcium carbonate equivalent (0-60in)	10%
Electrical conductivity (0-20in)	2 mmhos/cm
Sodium adsorption ratio (0-20in)	10
Soil reaction (1:1 water) (0-60in)	6.1 – 8.4
Subsurface fragment volume <=3" (20-60in)	2%
Subsurface fragment volume >3" (Depth not specified)	Not specified

Ecological dynamics

The reference plant communities of the Blackland are stable tall and midgrass prairies that were in dynamic equilibrium with the ecological forces that formed them. These forces included grazing by native wild herbivores, natural and anthropogenic fire, and periodic drought and wet cycles. Bison were the primary large ungulates that grazed but companion species included antelope and whitetail deer. The typical bison grazing pattern was short but very intense, followed by total deferment until herds migrated back into the area. Long deferments allowed the tallgrasses time to recover carbohydrate reserves and produce a seed crop. A fire regime and frequency of 3 to 8 years was likely and was a more important factor in shaping this prairie than was grazing.

The plant community for this site is dominated by tall and midgrasses. Major tallgrass species included big bluestem (Andropogon gerardii), yellow Indiangrass (Sorghastrum nutans), switchgrass (Panicum virgatum), eastern gamagrass (Tripsacum dactyloides), and Florida paspalum (Paspalum floridanum). Dominant midgrass species were little bluestem (Schizachyrium scoparium), brownseed paspalum (Paspalum plicatulum), sideoats grama (Bouteloua curtipendula), and meadow dropseed (Sporobolus compositus). Perennial forbs that were important to the site included sensitivebriars (Mimosa spp.), bundleflower (Desmanthus spp.), snoutbean (Rhynchosia spp), and gayfeather (Liatris spp.). Annual forbs occurred on this site in relatively high numbers in wet years and following intense grazing events by bison. Woody plants are nearly excluded from this site by competition from grasses and periodic intense fires. It should be noted however that some early accounts of this area showed a variable scattering of mesquite, live oak, and hackberry trees across the landscape. This is in keeping with the definition of true prairie which allows some large trees to be present but not enough to be termed savannah. The micro-highs and micro lows (gilgai micro-relief) on this site contribute to the diverse plant community. The micro highs are slightly drier and the micro lows slightly wetter. More wet-tolerant vegetation grows on the lower portions of the site while less wet-tolerant vegetation grows on the slightly higher portions of the site.

With the introduction of wild longhorn cattle in the late 1700’s and domestic cattle in the 1820’s, an era of heavy grazing began. During the Spanish Mission era of the 1600 to 1700’s, vast herds of cattle, horses, sheep, and goats were used for meat production for the missions. With no fences, these were free-roaming herds and animals could run free, and many escaped. Some portion of these herds took the place of bison once they were extirpated. This heavy grazing was exacerbated with the introduction of barbed wire and windmills in the 1880’s. Excessive grazing reduced or eliminated the tallgrass component and some midgrasses. As the site deteriorated, less palatable species such as brownseed paspalum, knotroot bristlegrass (Setaria parviflora), longspike tridens (Tridens strictus), and other shorter species like low panicums and paspalums increased.

As the tall and midgrasses decreased in composition and biomass production decreased, fuel for fires decreased as well, resulting in less frequent and lower intensity fires. Continued overuse of the site by livestock and the cessation of fire allowed woody plants to invade. These woody pioneers included mesquite (Prosopis glandulosa), huisache (Acacia farnesiana), Macartney rose (Rosa bracteata), eastern baccharis (Baccharis halamifolia), and Chinese tallow tree (Triadica sebifera). Increases in annual weeds, midgrasses such as three-awns (Aristida spp.), smutgrass (Sporobolus indicus), bahiagrass (Paspalum notatum), and the introduced bluestems (Bothriochloa spp.) also occur.

As thresholds from tall/midgrass prairie to mid/shortgrass prairie to shrub/tree/grassland complex are crossed, changes that have occurred which impact plant composition, biomass production, litter accumulation, and water infiltration and storage. These changes impact other natural ecological functions such as frequency and intensity of fire. The result has been conversion from a true prairie, to a wooded grassland, and eventually a woodland. In the heavily wooded state, total canopy cover may exceed 100 percent due to varying heights and multiple layers of woody species.

The resulting increase in woody cover signifies that thresholds have been crossed. Once these thresholds are crossed, restoration back to the reference plant community becomes more difficult and expensive. Even though the reference community may be restored through the use of a combination of practices, such as mechanical and herbicidal brush management, planned grazing, and fire, this community cannot be maintained without the use of these tools on a frequent basis.

State and transition model

More interactive model formats are also available. View Interactive Models
Click on state and transition labels to scroll to the respective text

Ecosystem states

1. Reference

2. Encroached

3. Converted

T1A	-	Absence of disturbance and natural regeneration over time
T1B	-	Clearing of native vegetation, followed by planting of improved forage species
R2A	-	Reintroduction of fire and regular disturbance return intervals
T2A	-	Clearing of vegetation, followed by planting improved forage species or annual crops
T3A	-	Absence of disturbance and natural regeneration over time

State 1
Reference

The Reference state is considered to be representative of pre-Euro settlement conditions. Wildfire, periodic drought and wet cycles, and grazing by native herbivores (bison, antelope and whitetail deer)were the major ecological drivers in this state. Under reference conditions wildfire occurred as frequently as every 3 to 8 years. Wildfire was an important disturbance in the reference state and resulted in the dominance of native, warm-season, tallgrasses.

Dominant plant species

big bluestem (Andropogon gerardii), grass
Indiangrass (Sorghastrum nutans), grass

Community 1.1
Native Tallgrass Prairie Community

The Reference Plant Community for the Blackland is a grassland composed of tall and midgrasses. Composition of tallgrasses make up over 60 percent of annual production, midgrasses approximately 30 percent, and associated grasses, forbs, shrubs and woody vines make up the remainder. Historically, bison grazing was intermittent, and fires were both frequent (3 to 8 years) and intense. Annual forbs occur in greater or lesser amounts in response to grazing intensity, fire, drought, or excessive precipitation. This prairie site was heavily grazed by large numbers of domestic livestock by the late 1800’s. Overgrazing without rest was exacerbated by the introduction of barbed wire fencing and water development. Overgrazing resulted in reduced production of biomass, reduced litter accumulation, loss of tallgrass and some midgrass species and reduction of fire frequency and intensity. Some mid and shortgrasses increased because of this overgrazing and eventually annual forbs and grasses.

Figure 8. 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	5850	7200	8550
Shrub/Vine	325	400	475
Forb	325	400	475
Tree	0	0	0
Total	6500	8000	9500

Figure 9. Plant community growth curve (percent production by month). TX7605, Tallgrass Prairie Community. Prairie community composed of dominant warm-season tallgrasses with some warm-season midgrasses..

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	4	12	24	24	8	5	12	4	3	2

Community 1.2
Tall/Midgrass Prairie

This community develops as heavy grazing removes the tallgrass component of the reference community. As tallgrasses decrease, midgrasses such as little bluestem, sideoats grama, brownseed paspalum, and longspike tridens increase. Reduced fuel loads result in reduced fire frequency and intensity. Annual and perennial forbs often increase because of decreased competition for sunlight and moisture. Continued heavy grazing over long periods of time further contributes to additional degradation and loss of more palatable midgrasses. Restoration to Community 1.1 is relatively simple and can be accomplished by prescribed grazing with appropriate stocking rates. The use of prescribed fire in conjunction with prescribed grazing enhances the recovery process.

Pathway 1.1A
Community 1.1 to 1.2

Heavy continuous grazing and lack of fire will transition the site to Community 1.2.

Pathway 1.2A
Community 1.2 to 1.1

Prescribed grazing with correct stocking rates and a return of fire will transition Community 1.2 back to the reference community.

State 2
Encroached

The Encroached state is characterized by an increase in long-lived woody plants. Widening of the disturbance return interval has allowed woody plants do dominate the visual aspect of the community, as well as ecological processes. Increasing runoff, reducing infiltration, and changing rates of litter accumulation, nutrient cycling and biomass production.

Dominant plant species

honey mesquite (Prosopis glandulosa), shrub
sweet acacia (Acacia farnesiana), shrub
Macartney rose (Rosa bracteata), shrub

Community 2.1
Mesquite/Huisache Grassland

This community has occurred because of abusive grazing, loss of fire, greatly altered water and energy cycles, and invasion of woody plants. A threshold has been crossed between plant community 1.2 and community 2.1. If prescribed grazing is implemented, fire re-introduced, and seedling woody plants controlled chemically and/or mechanically, this community can be quite productive for cattle and wildlife. This community can also be maintained indefinitely. To do so will require judicious grazing, periodic fire, and almost continuous application of herbicides on an individual plant basis. The Mesquite/Huisache community in this state will attract different better wildlife species than the previous state because of the increased amount of woody cover and the increased production of both perennial and annual forbs. With increased emphasis on whitetail deer, bobwhite quail, and Rio Grande turkey, many landowners choose to manage this state in this condition. Management such as prescribed fire and individual plant control of woody seedlings is still required if the site is to be maintained in this state.

Community 2.2
Mesquite/Huisache Complex

Over time, with continued heavy grazing, no fire, and no brush management, the site will be transformed into a woodland community with heavy influence of mesquite, huisache, and Macartney rose with canopies in excess of 90 percent. The herbaceous community is greatly reduced and is dominated by low panicums, paspalums, Texas wintergrass, gaping panicum, bentgrass, sedges, and annual forbs. Major inputs, both chemical and mechanical, are required to restore this community to a grassland or a savannah state. A common practice is the use of aerial applied herbicides to reduce the canopy, allow sunlight to penetrate to the soil surface, and grow enough herbaceous fuel loads for suitable burning. Aerial spraying is followed using prescribed fire to remove some of the woody vegetation and maintain semi-open wooded grassland for several years. Although these practices kill some of the woody vegetation, much of it remains and resprouts from the crown and in a relatively short period will attain a 90 percent canopy again. Often with this community, mechanical means such as rootplowing and raking are utilized, and the land is converted to cropland or tame pasture.

Pathway 2.1A
Community 2.1 to 2.2

Heavy grazing and lack of fire will cause an increase in brush density. The transition occurs when brush canopy cover is over 25 percent.

Pathway 2.2A
Community 2.2 to 2.1

To return to Community 2.1, brush density needs to be removed below 25 percent. Return of fire and prescribed grazing also help in this transition.

State 3
Converted

This state has been cleared and planted with introduced, forage species. Improved forage species are persistent and long-lived, contributing to the stability of this state. Important drivers include periodic grazing and management of woody species.

Dominant plant species

Bermudagrass (Cynodon dactylon), grass
beardgrass (Bothriochloa), grass
kleingrass (Panicum coloratum), grass

Community 3.1
Introduced/Native Species

A seedbed is prepared and the area is planted into grass. Because these soils are so productive, fertilizer has been inexpensive in the past, and precipitation is adequate, this site has been planted to bermudagrass, introduced bluestems, or kleingrass. If brush species are established, mechanical brush management must be utilized. Typically, rootplowing and raking are utilized to remove the woody vegetation, then a seedbed is prepared and the area is planted into grass. To maintain this seeded state, after approximately 3 to 5 years, herbicides must be used to control woody seedlings that seek to invade. Not only is there a long-lived seed source of mesquite, huisache, and other woody species, additional seeds are brought in by grazing animals and domestic livestock. Macartney rose seed and canes are also left behind following mechanical control and will re-establish in relatively short order. In the seeded state, if practices such as fertilizer application and weed control are stopped, prescribed grazing is applied, woody seedlings are managed, and prescribed burning is applied, this state will begin the reversion back to the Grassland State as seedlings of native species become established.

Community 3.2
Introduced/Native Species with Woody Seedlings

The transition from community 3.1 to 3.2 requires only time and the absence of woody seedling control. Due to the seed bank present in the soil and the constant addition of new seed from grazing/browsing animals and seed-eating birds, re-infestation of woody seedlings happens in a relatively short time period of 3 to 5 years. If woody seedlings are controlled on a semi-regular basis, this state can be maintained indefinitely, and the state can switch back and forth from 3.2 to 3.1. If this site has been planted to introduced species such as bermudagrass, introduced bluestems, or kleingrass, and fertilization and weed control is stopped and prescribed burning and prescribed grazing applied, pioneer native grasses and forbs will gradually begin to move back towards State 1.3. Some degree of woody plant control would be required for this to occur. If no woody plant management is practiced, then State 3.2 will revert to State 2.2 with a dominance of huisache and Macartney rose.

Pathway 3.1A
Community 3.1 to 3.2

With heavy grazing and no brush control, woody species will encroach the site.

Pathway 3.2A
Community 3.2 to 3.1

Seedling brush control, prescribed grazing, and possibly prescribed fire will transition the community back to 3.1.

Transition T1A
State 1 to 2

Heavy grazing, lack of fire, and brush invasion over 10 percent canopy signal the transition to State 2.

Transition T1B
State 1 to 3

Conversion signals this transition by preparing a seedbed and planting to pasture.

Restoration pathway R2A
State 2 to 1

Restoration occurs when brush management reduces the canopy cover below 10 percent, prescribed grazing restores correct stocking rates, and once grasses have created enough biomass, prescribed fire returns.

Transition T2A
State 2 to 3

Conversion signals this transition by clearing brush, preparing a seedbed, and planting to pasture.

Transition T3A
State 3 to 2

Without brush control to manage encroaching woody seedlings, the site will transition to State 2.

Additional community tables

Table 6. Community 1.1 plant community composition

Group	Common name	Symbol	Scientific name	Annual production (lb/acre)	Foliar cover (%)
Grass/Grasslike
1	Tallgrasses			3200–4700
	big bluestem	ANGE	Andropogon gerardii	3200–4700	–
	Florida paspalum	PAFL4	Paspalum floridanum	3200–4700	–
	switchgrass	PAVI2	Panicum virgatum	3200–4700	–
	little bluestem	SCSC	Schizachyrium scoparium	3200–4700	–
	Indiangrass	SONU2	Sorghastrum nutans	3200–4700	–
	eastern gamagrass	TRDA3	Tripsacum dactyloides	3200–4700	–
2	Tall/Midgrasses			1200–1650
	sideoats grama	BOCU	Bouteloua curtipendula	1200–1650	–
	vine mesquite	PAOB	Panicum obtusum	1200–1650	–
	brownseed paspalum	PAPL3	Paspalum plicatulum	1200–1650	–
	little bluestem	SCSCS	Schizachyrium scoparium var. scoparium	1200–1650	–
	large-spike bristlegrass	SEMA5	Setaria macrostachya	1200–1650	–
	composite dropseed	SPCOC2	Sporobolus compositus var. compositus	1200–1650	–
3	Midgrasses			600–950
	buffalograss	BODA2	Bouteloua dactyloides	600–950	–
	silver beardgrass	BOLAT	Bothriochloa laguroides ssp. torreyana	600–950	–
	Pan American balsamscale	ELTR4	Elionurus tripsacoides	600–950	–
	longtom	PADE24	Paspalum denticulatum	600–950	–
	marsh bristlegrass	SEPA10	Setaria parviflora	600–950	–
	white tridens	TRAL2	Tridens albescens	600–950	–
	longspike tridens	TRST2	Tridens strictus	600–950	–
4	Cool-season grasses			500–750
	sedge	CAREX	Carex	500–750	–
	Virginia wildrye	ELVI3	Elymus virginicus	500–750	–
	Texas wintergrass	NALE3	Nassella leucotricha	500–750	–
5	Shortgrasses			350–500
	Grass, annual	2GA	Grass, annual	350–500	–
	Grass, perennial	2GP	Grass, perennial	350–500	–
	fall witchgrass	DICO6	Digitaria cognata	350–500	–
	Scribner's rosette grass	DIOLS	Dichanthelium oligosanthes var. scribnerianum	350–500	–
	panicgrass	PANIC	Panicum	350–500	–
	crowngrass	PASPA2	Paspalum	350–500	–
Forb
6	Forbs			250–325
	Cuman ragweed	AMPS	Ambrosia psilostachya	250–325	–
	whitemouth dayflower	COER	Commelina erecta	250–325	–
	wedgeleaf prairie clover	DAEM2	Dalea emarginata	250–325	–
	Illinois bundleflower	DEIL	Desmanthus illinoensis	250–325	–
	velvet bundleflower	DEVE2	Desmanthus velutinus	250–325	–
	Engelmann's daisy	ENPE4	Engelmannia peristenia	250–325	–
	button eryngo	ERYU	Eryngium yuccifolium	250–325	–
	beeblossom	GAURA	Gaura	250–325	–
	coastal indigo	INMI	Indigofera miniata	250–325	–
	lespedeza	LESPE	Lespedeza	250–325	–
	dotted blazing star	LIPU	Liatris punctata	250–325	–
	littleleaf sensitive-briar	MIMI22	Mimosa microphylla	250–325	–
	powderpuff	MIST2	Mimosa strigillosa	250–325	–
	yellow puff	NELU2	Neptunia lutea	250–325	–
	fogfruit	PHYLA	Phyla	250–325	–
	white milkwort	POAL4	Polygala alba	250–325	–
	upright prairie coneflower	RACO3	Ratibida columnifera	250–325	–
	American snoutbean	RHAM	Rhynchosia americana	250–325	–
	least snoutbean	RHMI4	Rhynchosia minima	250–325	–
	violet wild petunia	RUNU	Ruellia nudiflora	250–325	–
	Drummond's skullcap	SCDR2	Scutellaria drummondii	250–325	–
	amberique-bean	STHE9	Strophostyles helvola	250–325	–
	Baldwin's ironweed	VEBA	Vernonia baldwinii	250–325	–
7	Forbs			60–90
	spiny chloracantha	CHSP11	Chloracantha spinosa	60–90	–
	eastern annual saltmarsh aster	SYSU5	Symphyotrichum subulatum	60–90	–
8	Forbs			15–60
	Forb, annual	2FA	Forb, annual	15–60	–
	Forb, perennial	2FP	Forb, perennial	15–60	–
	prairie broomweed	AMDR	Amphiachyris dracunculoides	15–60	–
	partridge pea	CHFAF	Chamaecrista fasciculata var. fasciculata	15–60	–
	croton	CROTO	Croton	15–60	–
	Dakota mock vervain	GLBIB	Glandularia bipinnatifida var. bipinnatifida	15–60	–
	camphorweed	HESU3	Heterotheca subaxillaris	15–60	–
	herb of the cross	VEOF	Verbena officinalis	15–60	–
Shrub/Vine
9	Shrubs			325–475
	sorrelvine	CITR2	Cissus trifoliata	325–475	–
	southern dewberry	RUTR	Rubus trivialis	325–475	–
	greenbrier	SMILA2	Smilax	325–475	–
Tree
10	Tree			0–1
	hackberry	CELTI	Celtis	0–1	–
	honey mesquite	PRGL2	Prosopis glandulosa	0–1	–
	live oak	QUVI	Quercus virginiana	0–1	–

Interpretations

Animal community

The Coastal Prairie communities support a wide array of animals. Cattle and many species of wildlife make extensive use of the site. White-tailed deer may be found scattered across the prairie and are found in heavier concentrations where woody cover exists. Feral hogs are present and at times abundant. Coyotes are abundant and fill the mammalian predator niche. Rodent populations rise during drier periods and fall during periods of inundation. Attwater’s pocket gophers are abundant and have an important impact on the ecology of the site. The badger is present but not abundant in locations at the southern extent of the site. Locally unique species alligators and bullfrogs.

The region is a major flyway for waterfowl and migrating birds. Hundreds of thousands of ducks, geese, and sandhill cranes abound during winter. Two important endangered species occur in the area, the whooping crane and Attwater’s prairie chicken. Many other species of avian predators including northern harriers, ferruginous hawks, red-tailed hawks, white-tailed kites, kestrels, and, occasionally, swallow-tailed kites utilize the vast grasslands. Many species of grassland birds use the site, including blue grosbeaks, dickcissels, eastern meadowlarks, several sparrows, including, vesper sparrow, lark sparrow, savannah sparrow, grasshopper sparrow, and Le Conte’s sparrow.

Hydrological functions

Peak rainfall periods occur in May and June from thunderstorms and in September and October from tropical systems. Rainfall events may be high (3 to 5 inches per event) and intense. Extended periods (45 to 60 days) of little to no rainfall during the growing season are common. Because of the flat topography of this site, erosion is minimal; however, on more sloping aspects (greater than 3 percent), erosion may be very significant. This site provides little water for aquifer recharge because when wet, infiltration is very slow.

Recreational uses

The site is used for camping when trees are present. Under proper management, when some woody species are present, the area will support large numbers of quail and is used for bird hunting. In a woodland state, white-tailed deer are present in large numbers and the site is hunted extensively. In the prairie state, large numbers of grassland birds are present and the area is used for bird watching.

Wood products

In the prairie state, no wood products are available. In a woodland state, the site may grow large numbers of large mesquite trees and these are often cut for firewood and barbecue wood.

Other products

Fruit from dewberries may be harvested. This site made up a major component of the historic Attwater’s Prairie Chicken habitat and extensive efforts are being made to reclaim it and re-introduce the prairie chicken.

Supporting information

Inventory data references

Vegetative data for this site was obtained from existing Range Site Descriptions and SCS-417 data. Nineteen SCS-417’s were available for this site in eight different counties. Extensive field work was done on-site to catalog the plant community. Several range-trained personnel with state and federal agencies and in private enterprise were consulted on the plant communities as well. Personal contact with ranchers and managers was utilized to ascertain the use of plants by both cattle and wildlife.

Other references

Allain, L., L. Smith, C. Allen, M. Vidrine, and J. B. Grace. 2006. A floristic quality assessment system for the Coastal Prairie of Louisiana. North American Prairie Conference, 19.

Allain, L., M. Vidrine, V. Grafe, C. Allen, and S. Johnson. 2000. Paradise lost: The coastal prairie of Louisiana and Texas. U.S. Fish and Wildlife Service, Layfayette, LA.

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. 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. and F. E. Smeins. 1991. Ecosystem-level processes. 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.

Baldwin, H. Q., J. B. Grace, W. C. Barrow, and F. C. Rohwer. 2007. Habitat relationships of birds overwintering in a managed coastal prairie. The Wilson Journal of Ornithology, 119(2):189-198.

Beasom, S. L, G. Proudfoot, and J. Mays. 1994. Characteristics of a live oak-dominated area on the eastern South Texas Sand Plain. In the Caesar Kleberg Wildlife Research Institute Annual Report, 1-2.

Berlandier, J. L. 1980. Journey to Mexico during the years 1826 to 1834: translated. Texas State Historical Associated and the University of Texas. Austin, TX.

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.

Bollaert, W. 1956. William Bollaert’s Texas. Edited by W. E. Hollon and R. L. Butler. University of Oklahoma Press, Norman, OK.

Bonnell, G. W. 1840. Topographical description of Texas: To which is added, an account of the Indian tribes. Clark, Wing, and Brown, Austin, TX.

Box, T. W. 1960. Herbage production on four range plant communities in South Texas. Journal of Range Management, 13:72-76.

Box, T. W. and A. D. Chamrad. 1966. Plant communities of the Welder Wildlife Refuge.

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.

Brite, T. R. 1860. Atascosa County. The Texas Almanac for 1861. Richardson and Co., Galveston, TX.

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.

Chamrad, A. D. and J. D. Dodd. 1972. Prescribed burning and grazing for prairie chicken habitat manipulation in the Texas coastal prairie. Tall Timbers Fire Ecology Conference Proceedings, 12:257-276.

Crawford, J. T. 1912. Correspondence from the British archives concerning Texas, 1837-1846. Edited by E. D. Adams. The Southwestern Historical Quarterly, 15:205-209.

Davis, R. B. and R. L. Spicer. 1965. Status of the practice of brush control in the Rio Grande Plain. Texas Parks and Wildlife Department Bulletin, 46.

Davis, W. B. 1974. The Mammals of Texas. Texas Parks and Wildlife Department Bulletin, 41.

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.

Drawe, D. L., A. D. Chamrad, and T. W. Box. 1978. Plant communities of the Welder Wildlife Refuge.

Drawe, D. L. and T. W. Box. 1969. High rates of nitrogen fertilization influence Coastal Prairie range. Journal of Range Management, 22:32-36.

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. and M. A. Alaniz. 1980. Fall and winter diets of feral pigs in south Texas. Journal of Range Management, 33:126-129.

Everitt, J. H. and D. L. Drawe. 1993. 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 used by livestock and wildlife. 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, 20.

Foster, W. C. 2010. Spanish Expeditions into Texas 1689-1768. University of Texas Press, Austin, TX.

Frost, C. C. 1995. Presettlement fire regimes in southeastern marshes, peatlands, and swamps. Tall Timbers Fire Ecology Conference Proceedings, 19:39-60.

Frost, C. C. 1998. Presettlement fire frequency regimes of the United States: A first approximation. Fire in ecosystem management: Shifting the paradigm from suppression to prescription. Tall Timbers Fire Ecology Conference Proceedings, 20:70-81.

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., D. D. Diamond, J. Rappole, and J. Norwine. 1990. The Coastal Sand Plain of Southern Texas. Rangelands, 12:337-340.

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.

Gould, F. W. 1975. The Grasses of Texas. Texas A&M University Press, College Station, TX.

Grace, J. B., T. M. Anderson, M. D. Smith, E. Seabloom, S. J. Andelman, G. Meche, E. Weiher, L. K. Allain, H. Jutila, M. Sankaran, J. Knops, M. Ritchie, and M. R. Willig. 2007. Does species diversity limit productivity in natural grassland communities? Ecology Letters, 10(8):680-689.

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.

Grace, J. B., L. Allain, C. Allen. 2000. Factors associated with plant species richness in a coastal tall-grass prairie. Journal of Vegetation Science, 11:443-452.

Graham, D. 2003. Kings of Texas: The 150-year saga of an American ranching empire. John Wiley & Sons, New York, NY.

Hamilton, W. and D. Ueckert. 2005. Rangeland woody plant control: Past, present, and future. Brush management: Past, present, and future, 3-16.

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.

Harcombe, P. A. and J. E. Neaville. 1997. Vegetation types of Chambers County, Texas. The Texas Journal of Science, 29:209-234.

Hatch, S. L., J. L. Schuster, and D. L. Drawe. 1999. Grasses of the Texas Gulf Prairies and Marshes. Texas A&M University Press, College Station, TX.

Heitschmidt, R. K. and J. W. Stuth. 1991. Grazing management: An ecological perspective. Timberline Press, Portland, OR.

Hughes, G.U. 1846. Memoir Description of a March of a Division of the United States Army under the Command of Brigadier General John E. Wool, From San Antonio de Bexar, in Texas to Saltillo, in Mexico. Senate Executive Document, 32.

Inglis, J. M. 1964. A history of vegetation of the Rio Grande Plains. Texas Parks and Wildlife Department Bulletin, 45.

Jenkins, J. H. 1973. The Papers of the Texas Revolution, 1835-1836. Presidential Press, Austin, TX.

Johnson, M. C. 1963. Past and present grasslands of southern Texas and northeastern Mexico. Ecology 44(3):456-466.

Joutel, H. 1906. Joutel’s journal of La Salle’s last voyage, 1686-1687. Edited by H. R. Stiles. Joseph McDonough, Albany, NY.

Kennedy, W. 1841. Texas: The rise, progress, and prospects of the Republic of Texas. Lincoln’s Inn, London, England.

Kimmel, F. 2008. Louisiana's Cajun Prairie: An endangered ecosystem. Louisiana Conservationist, 61(3):4-7.

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 Proceedings, 4:127-143.

Lehman, V. W. 1969. Forgotten Legions: Sheep in the Rio Grande Plain of Texas. Texas Western Press, El Paso, TX.

Lusk, R. M. 1917. A history of Constantine Lodge, No. 13, ancient free, and accepted Masons, Bonham, Texas. Favorite Printing Co., Hilbert, WI.

McDanield, H. F. and N. A. Taylor. 1877. The coming empire, or, two thousand miles in Texas on horseback. A. S. Barnes & Company, New York, NY.

McGinty A. and 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.

Mutz, J. L., T. J. Greene, C. J. Scifres, and B. H. Koerth. 1985. Response of Pan American balsamscale, soil, and livestock to prescribed burning. Texas Agricultural Experiment Station Bulletin, B-1492.

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. 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.

Palmer, G. R., T. E. Fulbright, and G. McBryde. 1995. Inland sand dune reclamation on the Coastal Sand Plain of Southern Texas. Caesar Kleberg Wildlife Research Institute Annual Report, 30-31.

Pickens, B., S. L. King, B. Vermillion, L. M. Smith, and L. Allain. 2009. Conservation Planning for the Coastal Prairie Region of Louisiana. A final report from Louisiana State University to the Louisiana Department of Wildlife and Fisheries and the U.S. Fish and Wildlife Service.

Prichard, D. 1998. Riparian area management: A user guide to assessing proper functioning condition and the supporting science for lotic areas. Bureau of Land Management, Denver, CO.

Rappole, J. H. and G. W. Blacklock. 1994. A field guide: Birds of Texas. Texas A&M University Press, College Station, TX.

Rappole, J. H. and G. W. Blacklock. 1985. Birds of the Texas Coastal Bend: Abundance and distribution. 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. 1975. Systems for improving McCartney rose infested coastal prairie rangeland. Texas Agricultural Experiment Station Bulletin, MP 1225.

Scifres, C. J. and W. T. Hamilton. 1993. Prescribed burning for brushland management: The South Texas example. Texas A&M Press, College Station, TX.

Shelby, C. 1933. Letters of an early American traveler: Mary Austin Holley, her life and her works, 1784-1846. Southwest Press, Dallas, TX.

Siemann, E., and W. E. Rogers. 2007. The role of soil resources in an exotic tree invasion in Texas coastal prairie. Journal of Ecology, 95(4):689-697.

Smith, L. M. 1996. The rare and sensitive natural wetland plant communities of interior Louisiana. Louisiana Natural Heritage Program, Baton Rouge, LA.

Smeins, F. E., D. D. Diamond, and W. Hanselka. 1991. Coastal prairie, 269-290. Ecosystems of the World: Natural Grasslands. Edited by R. T. Coupland. Elsevier Press, Amsterdam, Netherlands.

Stringham, T. K., W. C. Krueger, and P. L. Shaver. 2001. State and transition modeling: An ecological process approach. Journal of Range Management, 56(2):106-113.

Stutzenbaker, C. D. 1999. Aquatic and wetland plants of the Western Gulf Coast. University of Texas Press, Austin, TX.

Tharp, B. C. 1926. Structure of Texas vegetation east of the 98th meridian. University of Texas Bulletin, 2606.

Urbatsch, L. 2000. Chinese tallow tree Triadica sebifera (L.) Small. USDA-NRCS, National Plant Center, Baton Rouge, LA.

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.

Vidrine, M. F. 2010. The Cajun Prairie: A natural history. Cajun Prairie Habitat Preservation Society, Eunice, LA.

Vines, R. A. 1984. Trees of Central Texas. University of Texas Press, Austin, TX.

Vines, R. A. 1977. Trees of Eastern Texas. University of Texas Press, Austin, TX.

Warren, W. S. 1998. The La Salle Expedition to Texas: The journal of Henry Joutel, 1684-1687. Edited by W. C. Foster. Texas State Historical Association, 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. 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.

Weaver, J. E. and F. E. Clements. 1938. Plant ecology. McGraw-Hill, New York, NY.

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.

Wilbarger, J. W. 1889. Indian depredation in Texas. CreateSpace Independent Publishing Platform, Scotts Valley, CA.

Williams, L. R. and G. N Cameron. 1985. Effects of removal of pocket gophers on a Texas coastal prairie. The American Midland Naturalist Journal, 115:216-224.

Woodin, M. C., M. K. Skoruppa, and G. C. Hickman. 2000. Surveys of night birds along the Rio Grande in Webb County, Texas. Final Report, U.S. Fish and Wildlife Service, Corpus Christi, TX.

Wright, H.A. and A.W. Bailey. 1982. Fire Ecology: United States and Southern Canada. John Wiley & Sons, Inc., Hoboken, NJ.

Contributors

Stan Reinke

Approval

Bryan Christensen, 9/22/2023

Acknowledgments

The following personnel also contributed to the review process:
Jamey Douglas, RSS, NRCS, Temple, TX
Shanna Dunn, RSS, NRCS, Corpus Christi, TX
Mike Stellbauer, RMS, NRCS, Bryan, TX

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)	Mike Stellbauer, Zone RMS, NRCS, Bryan, TX
Contact for lead author
Date	07/18/2007
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:
Some water flow patterns are normal for this site due to landscape position and slopes.
Number and height of erosional pedestals or terracettes:
Pedestals or terracettes would have been very uncommon for this site.
Bare ground from Ecological Site Description or other studies (rock, litter, lichen, moss, plant canopy are not bare ground):
Less than 20 percent bare ground randomly distributed throughout.
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):
Small to medium-sized litter may move short distances during intense storms.
Soil surface (top few mm) resistance to erosion (stability values are averages - most sites will show a range of values):
Soil surface is resistant to erosion. Soil stability class range is expected to be 4 to 6.
Soil surface structure and SOM content (include type of structure and A-horizon color and thickness):
Soil surface structure is 10 to 60 inches thick with colors ranging from black to dark grayish brown with subangular blocky structure. SOM is 1 to 6 percent.
Effect of community phase composition (relative proportion of different functional groups) and spatial distribution on infiltration and runoff:
This true tallgrass prairie site with a combination of forbs, bunchgrasses and rhizomatous grasses which provides for optimum infiltration and little runoff under normal rainfall events.
Presence and thickness of compaction layer (usually none; describe soil profile features which may be mistaken for compaction on this site):
No evidence of compaction.
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 tallgrasses

Sub-dominant:
Warm-season midgrasses

Other:
Warm-season forbs Warm-season annual grasses Annual forbs

Additional:
Amount of plant mortality and decadence (include which functional groups are expected to show mortality or decadence):
Little apparent mortality or decadence for any functional groups.
Average percent litter cover (%) and depth ( in):
Expected annual annual-production (this is TOTAL above-ground annual-production, not just forage annual-production):
3,000 pounds per acre for below average moisture years to 8,000 pounds per acre for above average moisture years.
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:
Potential invasive species include Chinese tallow, huisache, mesquite, introduced bluestem, common bermudagrass, bahiagrass and Macartney rose.
Perennial plant reproductive capability:
All perennial plants should be capable of reproducing, except during prolonged drought conditions, heavy natural herbivory or intense wildfires.

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Ecosystem states

1. Reference

2. Encroached

3. Converted

T1A	-	Absence of disturbance and natural regeneration over time
T1B	-	Clearing of native vegetation, followed by planting of improved forage species
R2A	-	Reintroduction of fire and regular disturbance return intervals
T2A	-	Clearing of vegetation, followed by planting improved forage species or annual crops
T3A	-	Absence of disturbance and natural regeneration over time