Natural Resources
Conservation Service
Ecological site R150BY652TX
Southern Salt Marsh
Last updated: 9/22/2023
Accessed: 11/13/2024
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): 150B–Gulf Coast Saline Prairies
MLRA 150B is in the West Gulf Coastal Plain Section of the Coastal Plain Province of the Atlantic Plain and entirely in Texas. It makes up about 3,420 square miles. It is characterized by nearly level to gently sloping coastal lowland plains dissected by rivers and streams that flow toward the Gulf of Mexico. Barrier islands and coastal beaches are included. The lowest parts of the area are covered by high tides, and the rest are periodically covered by storm tides. Parts of the area have been worked by wind, and the sandy areas have gently undulating to irregular topography because of low mounds or dunes. Broad, shallow flood plains are along streams flowing into the bays. Elevation generally ranges from sea level to about 10 feet, but it is as much as 25 feet on some of the dunes. Local relief is mainly less than 3 feet. The towns of Groves, Texas City, Galveston, Lake Jackson, and Freeport are in the northern half of this area. The towns of South Padre Island, Loyola Beach, Corpus Christi, and Port Lavaca are in the southern half. Interstate 37 terminates in Corpus Christi, and Interstate 45 terminates in Galveston.
Classification relationships
USDA-Natural Resources Conservation Service, 2006.
-Major Land Resource Area (MLRA) 150B
Ecological site concept
Salt Marshes occur in areas less than 41 inches of mean annual precipitation and are closed depressions of the inland Coastal Plains exhibiting salt-tolerant vegetation.
Associated sites
| R150BY551TX |
Salty Prairie This site is on a higher landform and is drier. |
|---|---|
| R150BY716TX |
Wind Tidal Flat This site are in a similar position but are bare of vegetation or just have an algal mat. |
| R150BY651TX |
Salt Flat This site is on a slightly higher landform and is drier. |
Similar sites
| R150BY550TX |
Northern Salt Marsh This site is located in a higher precipitation regime. |
|---|
Table 1. Dominant plant species
| Tree |
Not specified |
|---|---|
| Shrub |
Not specified |
| Herbaceous |
(1) Spartina spartinae |
Physiographic features
The Salt Marsh occurs inland from the immediate ocean shoreline (strand) and often lies landward behind an additional zone of vegetated sand dunes. The landscape is typically very flat and interspersed with small drainages, small depressional areas, and variable sized open water bays. They may be crossed by streams or rivers that flow to the ocean. Sometimes high, linear ridges (cheniers) occur within the flat surface. The marshlands may extend a few hundred yards or up to several miles from the coast depending on the slope gradient.
Due to their location between the ocean and inland, the marshes are variously influenced by tides, saline substrates, and freshwater inflows. Generally, there is a gradient from saline to brackish to intermediate to freshwater marsh from the near ocean and bay influence to the inland uplands. This site was formed in deltaic, eolian or alluvium sediments. These soils are on nearly level coastal plains and depressional semi-marshy areas adjacent to the Gulf of Mexico. The slope is less than 1 percent. Elevation ranges from 1 to 15 feet.
Table 2. Representative physiographic features
| Landforms |
(1)
Coastal plain
> Flood plain
(2) Coastal plain > Depression (3) Coastal plain > Swale |
|---|---|
| Runoff class | Negligible to medium |
| Flooding duration | Long (7 to 30 days) |
| Flooding frequency | None to frequent |
| Ponding duration | Long (7 to 30 days) |
| Ponding frequency | None to frequent |
| Elevation | 1 – 45 ft |
| Slope | 1% |
| Ponding depth | 12 in |
| Water table depth | 40 in |
| Aspect | Aspect is not a significant factor |
Climatic features
The climate is predominately maritime, controlled by the warm and very moist air masses from the Gulf of Mexico. The climate along the upper coast of the barrier islands is subtropical subhumid and the climate on the lower coast of Padre Island is subtropical semiarid (due to high evaporation rates that exceed precipitation). Almost constant sea breezes moderate the summer heat along the coast. Winters are generally warm and are occasionally interrupted by incursions of cool air from the north. Spring is mild and damaging wind and rain may occur during spring and summer months. Tropical cyclones or hurricanes can occur with wind speeds of greater than 74 mph and have the potential to cause flooding from torrential rainstorms. Despite the threat of tropical storms, the storms are rare. Throughout the year, the prevailing winds are from the southeast to south-southeast.
The average annual precipitation is 45 to 57 inches in the northeastern half of this area, 26 inches at the extreme southern tip of the area, and 30 to 45 inches in the rest of the area. Precipitation is abundant in spring and fall in the southwestern part of the area and is evenly distributed throughout the year in the northeastern part. Rainfall typically occurs as moderate-intensity, tropical storms that produce large amounts of rain during the winter. The average annual temperature is 68 to 74 degrees F. The freeze-free period averages 340 days and ranges from 315 to 365 days.
Table 3. Representative climatic features
| Frost-free period (characteristic range) | 365 days |
|---|---|
| Freeze-free period (characteristic range) | 365 days |
| Precipitation total (characteristic range) | 26-32 in |
| Frost-free period (actual range) | 365 days |
| Freeze-free period (actual range) | 365 days |
| Precipitation total (actual range) | 26-34 in |
| Frost-free period (average) | 365 days |
| Freeze-free period (average) | 365 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) CORPUS CHRISTI NAS [USW00012926], Corpus Christi, TX
-
(2) PADRE IS NS [USC00416739], Padre Island Ntl Seashor, TX
-
(3) PORT MANSFIELD [USC00417184], Port Mansfield, TX
-
(4) PORT ISABEL CAMERON AP [USW00012957], Los Fresnos, TX
-
(5) PORT ISABEL [USC00417179], Port Isabel, TX
Influencing water features
Flooding will occur by overbank flow. Salt water will flood this site occasionally from tidal surges during tropical events.
Wetland description
These areas have hydric soils. Onsite investigation needed to determine local conditions.
Soil features
These are very deep mineral soils that vary in texture from sandy to loamy to clayey. Tidal influence and salty substrates produce saline to brackish conditions. However, at any given location, degree of salinity is a result of the local interaction of tidal influence, freshwater inflows, and substrate salt content. Soils are very poorly or poorly drained. Permeability varies with texture and depth of the water table but will generally be very slow or slow. Other features include neutral to strongly alkaline pH, krotovina (redistribution of horizons caused by animals), and redoximorphic accumulations and depletions. Soils correlated to this site include: Aransas, Lomalta, and Noria.
Table 4. Representative soil features
| Parent material |
(1)
Alluvium
–
igneous, metamorphic and sedimentary rock
(2) Eolian deposits – igneous, metamorphic and sedimentary rock |
|---|---|
| Surface texture |
(1) Clay (2) Fine sand |
| Family particle size |
(1) Fine (2) Sandy |
| Drainage class | Poorly drained to very poorly drained |
| Permeability class | Very slow to rapid |
| Soil depth | 80 in |
| Surface fragment cover <=3" | Not specified |
| Surface fragment cover >3" | Not specified |
| Available water capacity (0-60in) |
2 – 3 in |
| Calcium carbonate equivalent (0-60in) |
10% |
| Electrical conductivity (0-60in) |
8 – 20 mmhos/cm |
| Sodium adsorption ratio (0-60in) |
15 – 60 |
| Soil reaction (1:1 water) (0-60in) |
6.6 – 9 |
| Subsurface fragment volume <=3" (56-60in) |
2% |
Ecological dynamics
The environment is largely controlled by the Salt Marshes position between the ocean and inland upland sites. The generally flat, featureless plain is influenced by flooding of ocean tides, which vary seasonally and from year-to-year in their extent, duration, depth, and degree of salinity. In opposition to these ocean influences are freshwater inflows which move into the marsh as sheet flow from adjacent areas following precipitation events or result from flood overflow of streams that cross through the marsh from inland areas. Throughout the marsh, slight variations of a few inches in relief can produce noticeable changes in the plant community since minor variations in elevation can locally alter the salinity and water regime.
Within the marsh, many features add heterogeneity to the landscape and increase vegetation variability. Included are many small streams to large rivers that cross the marsh with their associated levees, oxbows, tidal guts, or drains that carry tidal waters inland. Depressional wetlands and small-to-large ridges that resulted from historic differential deposition and erosion within the this geomorphologically recent and active surface are present. Interspersed within the vegetated marsh may be open water bays and mudflats that vary in size, depth, and duration of standing water. The interaction of the tidal influence and the freshwater inflows are temporally and spatially variable which contribute to vegetative variation. This results from the local internal variation in elevation, as well as the rise in elevation from the coast inland, which may be subtle and gradual over long distances or can be abrupt and rapid over short distances.
All the variables contribute influences on the degree and rate of change of water and salinity regime moving inland. This correspondingly controls change in plant composition, which may be gradual and continuous when there is a minor elevation gradient or more zonal where it is more abrupt. The variation in salinity fluctuates as the site is further away from the ocean. Typically, saline water (greater than 10 parts per thousand of salt) is found closest to the ocean. Located further inland, they become brackish (3.5 to 10 parts per thousand), then intermediate (0.5 to 3.5 parts per thousand). Eventually, they arrive on the inland border as fresh marsh with less than 0.5 parts per thousand of salt.
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
State 1 submodel, plant communities
State 2 submodel, plant communities
State 1
Wet Grassland
Community 1.1
Mid/Tallgrass Prairie
The reference community is a mixture of mid and tallgrasses making up greater than 80 percent of the biomass. Dominant grasses would include marshhay cordgrass (Spartina patens), smooth cordgrass (Spartina alterniflora), seashore saltgrass (Distichlis spicata), and gulf cordgrass (Spartina spartinae). Interstitial graminoids include shoregrass (Monanthochloe littoralis), seashore paspalum, seashore dropseed (Sporobulus virginiucs), common reed (Phragmites australis), and bulrushes (Scirpus spp.). Forbs include dwarf glasswort (Salicornia virginica), sea lavender (Limonium carolinianum), and seacoast sumpweed (Iva annua). Woody plants are generally sparse in this community but may include sea oxeye (Borrichia frutescens) and wolfberry (Lycium carolinianum). Shifts in composition may occur due to changes in the water, salinity regimes, or in response to grazing impacts. Any of the factors may produce similar vegetation responses and thus careful assessment must be made to determine the cause of observed changes. Many of the graminoids become coarse and unpalatable at maturity and fire can be used to stimulate new, more palatable growth often increasing production. Heavy continuous grazing generally results in a decrease in marshhay cordgrass and smooth cordgrass while increasing the remaining species. Although season of grazing, as well as frequency and intensity, may shift the composition in several directions and interact in various ways with changes in the water and salinity regime to influence compositional changes.
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 | 3600 | 7400 | 11000 |
| Shrub/Vine | 200 | 300 | 450 |
| Forb | 200 | 300 | 450 |
| Tree | 0 | 0 | 0 |
| Total | 4000 | 8000 | 11900 |
Table 6. Ground cover
| Tree foliar cover | 0-1% |
|---|---|
| Shrub/vine/liana foliar cover | 0-1% |
| Grass/grasslike foliar cover | 80-90% |
| Forb foliar cover | 5-10% |
| Non-vascular plants | 0% |
| Biological crusts | 0% |
| Litter | 50% |
| Surface fragments >0.25" and <=3" | 0% |
| Surface fragments >3" | 0% |
| Bedrock | 0% |
| Water | 0% |
| Bare ground | 50% |
Figure 9. Plant community growth curve (percent production by month). TX7751, Midgrass Prairie Community. Open grassland plain composed of mid-grasses with seacoast bluestem and gulfdune paspalum dominate the site..
| 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 | 15 | 20 | 15 | 10 | 10 | 15 | 6 | 4 | 0 |
Community 1.2
Midgrass/Forb Prairie
This community is similar to the Mid/Tallgrass Prairie Community (1.1) but has a shift in dominance to a mixture of marshhay cordgrass, smooth cordgrass, gulf cordgrass, and seashore saltgrass. In addition, common reed, seashore dropseed, and seashore paspalum decrease in abundance. Shoregrass, sea ox-eye, devil-weed/spiny Chlorancantha (Chloracantha spinosa), and coffeebean increase in abundance. This shift in composition can be driven by heavy grazing but may occur during extended periods of high salinity. Improved salinity conditions and proper grazing management will help restore reference conditions.
Community 1.3
Forb Dominant
With continued heavy grazing and/or severe persistent high salinities the grass cover of this community begins to open and the amount of bare ground increases along with an increase of forbs. Spiny chloracantha, sea ox-eye, ragged marsh-elder sumpweed (Hedosyne ambrosiifolia), seacoast sumpweed, bulrushes, eastern baccharis, and assorted sedges and rushes become dominant. When the site is dominated by these species it becomes more difficult to return it to the Midgrass/Tallgrass Prairie Community (1.1) or the Midgrass/Forb Community (1.2) by grazing management. Pest management, brush management, and prescribed grazing in combination may be necessary to improve the condition.
Pathway 1.1A
Community 1.1 to 1.2
Heavy grazing will impact the site negatively and cause a transition to Community 1.2.
Pathway 1.2A
Community 1.2 to 1.1
Grazing management or reduction of salinity transition the site back to reference conditions.
Pathway 1.2B
Community 1.2 to 1.3
Continued overgrazing and/or prolonged high salinity exposure transition the site to Community 1.3.
Pathway 1.3A
Community 1.3 to 1.2
Prescribed grazing, pest management, and/or lowered salinity conditions transition the site back to 1.2.
State 2
Mudflat
Community 2.1
Mudflat
In the extreme, the site would be denude of vegetation. But in most cases, gulf cordgrass, saltwort, glasswort, seashore saltgrass, and sea-oxeye will be present. Grazing is the main driver of this condition, but other factors like effects from hurricanes with flooding or tidal inundation also have influence. Most of the reference species still found tend to reproduce by vegetative means. The rate of recovery to a vegetated state will be controlled by the density and vigor of these remnant plants, as well as the size of the mudflat. Recovery may be very slow as reseeding is generally not feasible due to lack of a seed source and difficulty of establishment. Some acquisition of plants may be done naturally by wildlife transfer. Planting of vegetative materials can assist in accelerating the recovery process but may not be feasible over large areas. Generally, rest from further disturbance may be the only reasonable approach to recovery but may require several years.
Transition T1A
State 1 to 2
Heavy overgrazing or a hurricane can cause the transition to State 2. The Forb Dominant Community (1.3) is at risk to transition if the site is not allowed to revegetate.
Restoration pathway R2A
State 2 to 1
Revegetation of the natural plant system is necessary to restore the Wet Grassland State (1). Revegetating can be difficult because it requires sprigging as seed sources are usually not viable. Time and restriction from further disturbance is generally the most feasible option.
Additional community tables
Table 7. Community 1.1 plant community composition
| Group | Common name | Symbol | Scientific name | Annual production (lb/acre) | Foliar cover (%) | |
|---|---|---|---|---|---|---|
|
Grass/Grasslike
|
||||||
| 1 | Midgrasses | 2000–5500 | ||||
| saltmeadow cordgrass | SPPA | Spartina patens | 1000–3500 | – | ||
| smooth cordgrass | SPAL | Spartina alterniflora | 1000–3500 | – | ||
| 2 | Mid/Tallgrasses | 2000–5000 | ||||
| saltgrass | DISP | Distichlis spicata | 1000–2500 | – | ||
| gulf cordgrass | SPSP | Spartina spartinae | 1000–2500 | – | ||
| seashore dropseed | SPVI3 | Sporobolus virginicus | 500–1500 | – | ||
| shoregrass | MOLI | Monanthochloe littoralis | 500–1500 | – | ||
| seashore paspalum | PAVA | Paspalum vaginatum | 500–1500 | – | ||
| switchgrass | PAVI2 | Panicum virgatum | 0–1500 | – | ||
| common reed | PHAU7 | Phragmites australis | 500–1500 | – | ||
| chairmaker's bulrush | SCAM6 | Schoenoplectus americanus | 500–1500 | – | ||
| sedge | CAREX | Carex | 500–1000 | – | ||
| flatsedge | CYPER | Cyperus | 500–1000 | – | ||
| southern cattail | TYDO | Typha domingensis | 500–1000 | – | ||
| marsh bristlegrass | SEPA10 | Setaria parviflora | 250–750 | – | ||
| Indiangrass | SONU2 | Sorghastrum nutans | 0–500 | – | ||
| longtom | PADE24 | Paspalum denticulatum | 0–500 | – | ||
| eastern gamagrass | TRDA3 | Tripsacum dactyloides | 0–500 | – | ||
|
Forb
|
||||||
| 3 | Forbs | 200–450 | ||||
| alligatorweed | ALPH | Alternanthera philoxeroides | 50–100 | – | ||
| Cuman ragweed | AMPS | Ambrosia psilostachya | 50–100 | – | ||
| turtleweed | BAMA5 | Batis maritima | 50–100 | – | ||
| herb of grace | BAMO | Bacopa monnieri | 50–100 | – | ||
| bushy seaside tansy | BOFR | Borrichia frutescens | 50–100 | – | ||
| spiny chloracantha | CHSP11 | Chloracantha spinosa | 50–100 | – | ||
| seaside heliotrope | HECUO2 | Heliotropium curassavicum var. obovatum | 50–100 | – | ||
| narrowleaf marsh elder | IVAN | Iva angustifolia | 50–100 | – | ||
| Jesuit's bark | IVFR | Iva frutescens | 50–100 | – | ||
| Virginia saltmarsh mallow | KOVI | Kosteletzkya virginica | 50–100 | – | ||
| sea lavender | LIMON | Limonium | 50–100 | – | ||
| dwarf saltwort | SABI | Salicornia bigelovii | 50–100 | – | ||
| slender seapurslane | SEMA3 | Sesuvium maritimum | 50–100 | – | ||
| annual seepweed | SULI | Suaeda linearis | 50–100 | – | ||
| southwestern annual saltmarsh aster | SYEX | Symphyotrichum expansum | 50–100 | – | ||
| perennial saltmarsh aster | SYTE6 | Symphyotrichum tenuifolium | 50–100 | – | ||
|
Shrub/Vine
|
||||||
| 4 | Shrubs/Vines | 200–450 | ||||
| eastern baccharis | BAHA | Baccharis halimifolia | 50–300 | – | ||
| Carolina desert-thorn | LYCA2 | Lycium carolinianum | 50–300 | – | ||
| bigpod sesbania | SEHE8 | Sesbania herbacea | 50–300 | – | ||
Interpretations
Animal community
The animal communities of the Coastal Prairie communities are influenced by fresh and salt water inundations. 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 become abundant. Coyotes are abundant and fill the mammalian predator niche. Rodent populations rise during drier periods and fall during periods of inundation. Alligators are locally abundant and make frequent use of the marshes depending on salt concentrations in the marshes.
The region is a major flyway for waterfowl and migrating birds. Hundreds of thousands of ducks, geese, and sandhill cranes abound during winter. Whooping cranes are an important endangered species that occur in the area, especially near Aransas National Wildlife Refuge. Northern harriers are common predatory birds seen patrolling marshes. Curlews, plovers, sandpipers, and willets are shorebirds that make use of the tidal areas. Seagulls and terns are plentiful throughout the year trolling the shores as well. Further inland, rails, gallinules, and moorhens make use of the brackish marshes.
Hydrological functions
Infiltration into the soils of this site is variable corresponding to the texture. However, because of the level terrain and proximity to the Gulf of Mexico, this site may be inundated periodically.
Supporting information
Inventory data references
Information presented was derived from the Range Site Description, NRCS clipping data, literature, field observations, and personal contacts with range-trained personnel.
Other references
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. Grazing Management: An Ecological Perspective. Edited by R.K. Heischmidt and J.W. Stuth. Timber Press, Portland, OR.
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.
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.
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.
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.
Butzler, R. E. 2006. The Spatial and Temporal Patterns of Lycium carolinianum Walt. M. S. Thesis. Texas A&M, College Station, TX.
Chabreck, R. H. 1972. Vegetation, water and soil characteristics of the Louisiana coastal region. Louisiana State University Agriculture Experiment Station Bulletin, 664.
Davis, W. B. 1974. The Mammals of Texas. Texas Parks and Wildlife Department Bulletin, 41.
Drawe, D. L., A. D. Chamrad, and T. W. Box. 1978. Plant communities of the Welder Wildlife Refuge. The Welder Wildlife Refuge, Sinton, TX.
Drawe, D. L., K. R. Kattner, W. H. McFarland, and D. D. Neher. 1981. Vegetation and soil properties of five habitat types on north Padre Island. Texas Journal of Science, 33:145-157.
Everitt, J. H., D. L. Drawe, and R. I. Leonard. 2002. Trees, Shrubs, and Cacti 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, 20.
Frost, C. C. 1995. Presettlement fire regimes in southeastern marshes, peatlands, and swamps. Tall Timbers Fire Ecology Conference Proceedings, 19:39-60.
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.
Gosselink, J.D., C.L. Cordes, and J.W. Parsons. 1979. An. Ecological characterization study of the Chenier Plain Coastal Ecosystem of Louisiana and Texas. U.S. Fish and Wildlife Service, Office of Biological Services, Washington, D.C.
Gould, F. W. 1975. The Grasses of Texas. Texas A&M University Press, College Station, TX.
Gould, F. W. and T. W. Box. 1965. Grasses of the Texas Coastal Bend. 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. Brush management: Past, present, and future, 3-16.
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.
Johnson, M. C. 1963. Past and present grasslands of southern Texas and northeastern Mexico. Ecology 44(3):456-466.
Lehman, V. W. 1965. Fire in the range of Attwater’s prairie chicken. Tall Timbers Fire Ecology Conference Proceedings, 4:127-143.
Mann, C. 2004. 1491: New Revelations of the Americas before Columbus. Vintage Books, New York City, NY.
Mapston, M. E. 2007. Feral Hogs in Texas. Texas Agrilife Extension Bulletin, B-6149
McAtee, J. W., C. J. Scifres, D. L. and Drawe. 1979. Digestible energy and protein content of gulf cordgrass following burning or shredding. Journal of Range Management, 376-378.
McGowen, J. H., L. F. Brown, T. J. Evans, W. L. Fisher, and C. G. Groat. 1976. Environmental geologic atlas of the Texas Coastal Zone-Bay City-Freeport area. The University of Texas at Austin, Bureau of Economic Geology, Austin, TX.
Miller, D. L., F. E Smeins, and J. W. Webb. 1998. Response of a Texas Distichlis spicata coastal marsh following Lesser Snow Goose herbivory. Aquatic Botany, 61:301-307.
Miller, D. L., F. E. Smeins, and J. W. Webb. 1996. Mid-Texas coastal marsh change (1939-1991) as influenced by Lesser Snow Goose herbivory. Journal of Coastal Research, 12:462-476.
Miller, D. L., F. E. Smeins, J. W. Webb, and M. T. Longnecker. 1997. Regeneration of Scirpus americanus in a Texas coastal marsh following Lesser Snow Goose herbivory. Wetlands, 17:31-42.
Oefinger, R. D. and C. J. Scifres. 1977. Gulf cordgrass production, utilization, and nutritional value following burning. Texas Agricultural Experiment Station Bulletin, B-1176.
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, 1994-1995.
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. 1985. Birds of the Texas Coastal Bend: Abundance and distribution. Texas A&M University Press, 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., J. W. McAtee, and D. L. Drawe 1980. Botanical, edaphic, and water relationships of gulf cordgrass (Spartina spartinae [Trin.] Hitchc.) and associated communities. The Southwestern Naturalist, 25(3):397-409.
Shiflet, T. N. 1963. Major ecological factors controlling plant communities in Louisiana marshes. Journal of Range Management, 16:231-235.
Singleton, J. R. 1951. Production and utilization of waterfowl food plants on the east Texas gulf coast. Journal of Wildlife Management, 15:46-56.
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.
Smeins, F. E., S. Fuhlendorf, and C. Taylor, Jr. 1997. Environmental and land use changes: A long term perspective. Juniper Symposium, 1-21.
Snyder, R. A. and C. L. Boss. 2002. Recovery and stability in barrier island plant communities. Journal of Coastal Research, 18:530-536.
Stoddart, L. A., A. D. Smith, and T. W. Box. 1975. Range management. McGraw-Hill Book Co., New York, NY.
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.
Thornthwaite, C. W. 1948. An approach towards a rational classification of climate. Geographical Review, 38: 55-94.
Thurow, T. L. 1991. Hydrology and erosion. 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, 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.
Vines, R. A. 1977. Trees of Eastern Texas. University of Texas Press, Austin, TX.
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. 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.
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.
Weaver, J. E. and F. E. Clements. 1938. Plant ecology. McGraw-Hill, New York, NY.
Williams, A. M., R. A. Feagin, W.K. Smith, and N. L. Jackson. 2009. Ecosystem impacts of Hurricane Ike on Galveston Island and Bolivar Peninsula: Perspectives of the coastal barrier island network (CBIN). Shore and Beach, 7(2):1-5.
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.
Wright, H.A. and A.W. Bailey. 1982. Fire Ecology: United States and Southern Canada. John Wiley & Sons, Inc., Hoboken, NJ.
Contributors
Dr. Fred E. Smeins, Professor, Texas A&M University, College Station, TX
Approval
Bryan Christensen, 9/22/2023
Acknowledgments
Reviewers:
Justin Clary, RMS, NRCS, Temple, TX
Shanna Dunn, RSS, NRCS, Corpus Christi, TX
Vivian Garcia, RMS, NRCS, Corpus Christi, TX
Jason Hohlt, RMS, NRCS, Kingsville, TX
Mark Moseley, RMS, NRCS, San Antonio, TX
Tim Reinke, RMS, NRCS, Temple, TX
Site Development and Testing Plan:
Future work, as described in a Project Plan, to validate the information in this Provisional Ecological Site Description is needed. This will include field activities to collect low, medium and high-intensity sampling, soil correlations, and analysis of that data. Annual field reviews should be done by soil scientists and vegetation specialists. A final field review, peer review, quality control, and quality assurance reviews of the ESD will be needed to produce the final document. Annual reviews of the Project Plan are to be conducted by the Ecological Site Technical Team.
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) | |
|---|---|
| Contact for lead author | |
| Date | 09/24/2023 |
| Approved by | Bryan Christensen |
| Approval date | |
| Composition (Indicators 10 and 12) based on | Annual Production |
Indicators
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Number and extent of rills:
-
Presence of water flow patterns:
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Number and height of erosional pedestals or terracettes:
-
Bare ground from Ecological Site Description or other studies (rock, litter, lichen, moss, plant canopy are not bare ground):
-
Number of gullies and erosion associated with gullies:
-
Extent of wind scoured, blowouts and/or depositional areas:
-
Amount of litter movement (describe size and distance expected to travel):
-
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):
-
Effect of community phase composition (relative proportion of different functional groups) and spatial distribution on infiltration and runoff:
-
Presence and thickness of compaction layer (usually none; describe soil profile features which may be mistaken for compaction on this site):
-
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:
Sub-dominant:
Other:
Additional:
-
Amount of plant mortality and decadence (include which functional groups are expected to show mortality or decadence):
-
Average percent litter cover (%) and depth ( in):
-
Expected annual annual-production (this is TOTAL above-ground annual-production, not just forage annual-production):
-
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:
-
Perennial plant reproductive capability:
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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.
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