Natural Resources
Conservation Service
Ecological site R030XB221CA
Loamy Fan Remnants And Pediments
Accessed: 04/18/2024
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): 030X–Mojave Basin and Range
MLRA Description:
Major Land Resource Area (MLRA) 30, Mojave Desert, is found in southern California, southern Nevada, the extreme southwest corner of Utah and northwestern Arizona within the Basin and Range Province of the Intermontane Plateaus. The climate of the area is hot (primarily hyperthermic and thermic; however at higher elevations, generally above 5000 feet, mesic, cryic and frigid) and dry (aridic). Elevations range from below sea level to over 12,000 feet in the higher mountain areas found within the MLRA. Due to the extreme elevational range found within this MLRA, Land Resource Units (LRUs) were designated to group the MLRA into similar land units.
LRU Description:
This LRU (designated by ’XB’) is found across the eastern half of California, much of the mid-elevations of Nevada, the southernmost portions of western Utah, and the mid-elevations of northwestern Arizona. Elevations range from 1800 to 5000 feet and precipitation ranges from 4 to 9 inches per year, but is generally between 5-6 inches. This LRU is characterized primarily by the summer precipitation it receives, ranging from 18 – 35% but averages 25%. Summer precipitation falls between July and September in the form of rain, and winter precipitation falls starting in November and ends between February and March, also mostly in the form of rain; however it does receive between 0 and 3 inches of snow, with an average of 1 inch. The soil temperature regime is thermic and the soil moisture regime is typic-aridic. Vegetation includes creosote bush, burrobush, Nevada jointfir, ratany, Mojave yucca, Joshua tree, chollas, cactus, big galleta grass and several other warm season grasses. At the upper portions of the LRU, plant production and diversity are greater and blackbrush is a common dominant shrub.
Ecological Site Concept -
This ecological site is found on eroded fan remnants and dissected pediments at elevations of 2230 to 4040 feet. Soils have a warm thermic temperature regime, loamy textures and have a well-developed argillic horizon beginning within 1 to 8 inches of the soil surface that occurs over hard bedrock or a duripan. This site is located close to the MLRA30-31 (Mojave – Lower Colorado Desert) boundary.
Production Reference Value (RV) is 297 pounds per acre and ranges from 195 to 402 pounds per acre depending on annual precipitation. The reference plant community is co-dominated by blackbrush (Coleogyne ramosissima) and burrobush (Ambrosia dumosa), and secondary shrub diversity is high. This ecological site is found at relatively low elevations for blackbrush in the Mojave Desert. A well-developed argillic horizon significantly increases soil moisture holding capacity, which allows blackbrush to be a dominant species despite low elevations. The argillic horizon also enhances habitat for the shallow-rooted burrobush. The transitional climatic location and dissected topography enhances shrub diversity.
Data in the following sections is based on all components (major and minor) correlated with this ecological site.
Associated sites
| R030XB218CA |
Moderately Deep To Very Deep Loamy Fan Remnants This ecological site is found on adjacent fan aprons on fan remnants. Burrobush (Ambrosia dumosa) and creosote bush (Larrea tridentata) dominate. |
|---|---|
| R030XB220CA |
Very Shallow Duripan Fan Remnants This ecological site is found on adjacent fan remnants with very shallow soils to a duripan. Sparse vegetation is dominated by burrobush (Ambrosia dumosa) and lotebush (Ziziphus obtusifolia). |
| R030XB225CA |
Warm Sloping Pediments This ecological site occurs on adjacent shallow pediments. Burrobush (Ambrosia dumosa) and Hall's shrubby spurge (Tetracoccus hallii) dominate. |
Similar sites
| R030XB189CA |
Shallow Cool Hills This ecological site is found on pediments at higher elevations and is co-dominated by creosote bush (Larrea tridentata). |
|---|---|
| R030XB166CA |
Dissected Pediment, Cool This ecological site is found on pediments at higher elevations. California juniper (Juniperus californica) is an important species and burrobush (Ambrosia dumosa) is trace if present. |
| R030XB220CA |
Very Shallow Duripan Fan Remnants This ecological site occurs on fan remnants with shallow soils to a duripan. Production is lower, blackbrush (Coleogyne ramosissima) is not an important species and burrobush (Ambrosia dumosa) and lotebush (Ziziphus obtusifolia) dominate. |
Table 1. Dominant plant species
| Tree |
Not specified |
|---|---|
| Shrub |
(1) Coleogyne ramosissima |
| Herbaceous |
Not specified |
Physiographic features
This ecological site occurs on pediments and fan remnants at elevations of 2230 to 4040 feet. Slopes range from 2 to 30 percent. Runoff class is low to medium.
Table 2. Representative physiographic features
| Landforms |
(1)
Pediment
(2) Fan remnant |
|---|---|
| Flooding frequency | None |
| Ponding frequency | None |
| Elevation | 2,230 – 4,040 ft |
| Slope | 2 – 30% |
| Aspect | Aspect is not a significant factor |
Climatic features
The climate on this site is characterized by cool, somewhat moist winters and hot, somewhat moist summers, with approximately 60 percent of precipitation falling as rain between November and March, and approximately 30 percent falling as rain between July and October (slightly higher than the average for the XB LRU). Summer precipitation falls as heavy monsoonal events, while winter precipitation is spread out over a longer time period. The average annual precipitation ranges from 4 to 7 inches. Mean annual air temperature is 63 to 68 degrees F, and the frost free period ranges from 270 to 320 days per year.
Maximum and minimum monthly climate data for this ESD were generated by the Climate Summarizer
(http://www.nm.nrcs.usda.gov/technical/handbooks/nrph/Climate_Summarizer.xls) using data
from the following climate stations:
44405 Joshua Tree, California (Period of record = 1959 to 2011) [1]
LTHC1 Lost Horse, Joshua Tree National Park (Period of record = 1991 to 2011) [1]
49099, Twentynine Palms, California (Period of record = 1935 – 2011) [1]
The data from multiple weather were combined to most accurately reflect the climatic conditions of this ecological site. The Lost Horse and Joshua Tree weather stations have colder temperatures and less summer precipitation than this ecological site. The Twentynine Palms weather station has hotter temperatures and less total precipitation than this ecological site.
Table 3. Representative climatic features
| Frost-free period (average) | 320 days |
|---|---|
| Freeze-free period (average) | 0 days |
| Precipitation total (average) | 7 in |
Figure 2. Monthly precipitation range
Figure 3. Monthly average minimum and maximum temperature
Influencing water features
Soil features
The soils associated with this ecological site are shallow to deep, and formed in residuum derived from granitoid, or in alluvium derived from granitoid. Surface textures are gravelly fine sandy loam and sandy loam with loamy subsurface textures. These soils have an argillic horizon beginning at 0.5 to 10 inches below the soil surface. For gravel-sized rock fragments (less than 3 inches in diameter), the percent surface cover range from 15 to 47 percent, and larger fragments are 3 to 7 percent. Subsurface volume of gravel-sized rock fragments (for a depth of 0 to 59 inches) is 5 to 30 percent, and larger rock fragments are 0 to 15 percent.
The soils that are associated with this ecological site are: Grinder (loamy, mixed, superactive, thermic Lithic Haplargids); Pinkcan (fine-loamy, mixed, superactive, thermic Duric Petroargids); and Popups (coarse-loamy, mixed, superactive, thermic Argidic Argidurids).
The Grinder soils occur on pediments, and are very shallow over unweathered, slightly fractured bedrock. An argillic horizon begins at 0.5 inches below the surface, and is 7.5 inches thick. The Pinkcan soils occur on fan remnants and are very deep. An argillic horizon begins at 0.5 to 2.5 inches, and is approximately 24 inches thick. A duripan begins at 40 to 59 inches. The Popups soils also occur on fan remnants, but are moderately deep to a duripan (20 to 40 inches to top of pan). An argillic horizon begins at 8 inches below the soil surface, and is approximately 26 inches thick.
This ecological site is correlated with the following map units and soil components in the Joshua Tree National Park Soil Survey:
4625;Grinder-Pinkcan complex, 4 to 30 percent slopes;Grinder;50; Pinkcan;cool;15
4260;Minhoyt-Corbilt association, 2 to 8 percent slopes;Popups;cool;9
Table 4. Representative soil features
| Parent material |
(1)
Residuum
–
granite
(2) Alluvium – granite |
|---|---|
| Surface texture |
(1) Gravelly fine sandy loam (2) Sandy loam |
| Family particle size |
(1) Loamy |
| Drainage class | Well drained |
| Permeability class | Very slow to moderate |
| Soil depth | 8 – 59 in |
| Surface fragment cover <=3" | 15 – 47% |
| Surface fragment cover >3" | 3 – 7% |
| Available water capacity (0-40in) |
0.7 – 5.9 in |
| Calcium carbonate equivalent (0-40in) |
1% |
| Electrical conductivity (0-40in) |
Not specified |
| Sodium adsorption ratio (0-40in) |
Not specified |
| Soil reaction (1:1 water) (0-40in) |
6.6 – 8.4 |
| Subsurface fragment volume <=3" (Depth not specified) |
5 – 30% |
| Subsurface fragment volume >3" (Depth not specified) |
15% |
Ecological dynamics
Abiotic factors
The abiotic factors driving this site are an eroded fan remnant and dissected pediment landscape, well developed soils with a thick argillic horizon, and warm thermic soil temperatures. This ecological site occurs on eroded fan remnants and dissected pediments at elevations of 2230 to 4040 feet. Soils have a warm thermic temperature regime, loamy textures and have a well-developed argillic horizon beginning within 10 inches of the soil surface that occurs over bedrock or a duripan. This significantly increases soil moisture holding capacity at near surface depths, which allows the shallow-rooted blackbrush to be a dominant species despite a temperature range near the upper limits for blackbrush. Blackbrush does not thrive in these warmer climates, and individuals are stunted and less competitive than in cooler climates, and site diversity is higher than is typical for a blackbrush-dominated community (Brooks and Matchett 2003, Pendleton and Meyer 2004). Since this site represents the warmest extension of the range of blackbrush, it is significant in terms of blackbrush adaptation and response to climate change. At lower elevations warmer temperatures reduce soil moisture so that it is too low to support blackbrush, and temperatures are not cold enough for the cold stratification that blackbrush seeds require for germination (Pendleton et al. 1995, Lei 1997, Pendleton and Meyer 2004). However, blackbrush demonstrates ecotypic variation with seed germination, with plants at warmer sites requiring less time for cold-stratification (Lei 1997, Pendleton and Meyer 2004). This trait has likely allowed blackbrush to expand its range to lower elevations in response to historic climate change (Cole and Webb 1985). Conservation of populations at climate extremes is thus important for facilitating blackbrush adaptation to modern day climate change.
Increased soil moisture holding capacity also enhances habitat for the shallow-rooted burrobush. Burrobush is a short-lived, shallow-rooted, drought-deciduous shrub that co-exists with creosote bush over vast areas of North American Deserts. Burrobush becomes more dominant on older soils with greater horizon development, because well-developed argillic, petrocalcic or duripans impede water infiltration, and increase the temporal availability of water at shallower depths.
This ecological site occurs at the southern edge of the Mojave Desert (the Mojave Desert – Lower Colorado Desert or MLRA30-31 boundary). Thus, it has a relatively warm climate with few frost days, and it represents a transition from a warm desert where winter precipitation is dominant, to a hot desert where summer precipitation is much more significant. Blackbrush is widespread in the Great Basin Desert and at mid-elevations in the Mojave Desert, and burrobush and is widespread species in the Mojave and Colorado Deserts. The transitional climatic position of this ecological site increases shrub diversity, with several species more typical of climates receiving more precipitation than the Mojave Desert are important species in this site, including Hall’s shrubby spurge (Tetracoccus hallii), lotebush (Ziziphus obtusifolia), Parry’s beargrass (Nolina parryi), and mouse’s eye (Bernardia myricifolia). Cactus species, which are efficient at utilizing the increased summer moisture received by this ecological site, are prevalent. The topography of the dissected pediment and eroded fan remnant landforms provides contrasting and localized areas of soil erosion and deposition, and run-off and run-on, which further supports a diverse plant community.
Disturbance Dynamics
The primary disturbances influencing this ecological site are drought, invasion by non-native annual plants, and fire, all of which interact. Drought is an important shaping force in Mojave Desert plant communities (Webb et al. 2003, Hereford et al. 2006). Short-lived perennial shrubs and perennial grasses demonstrate the highest rates of mortality (Webb et al. 2003, Bowers 2005, Hereford et al. 2006, Miriti et al. 2007) and annual species remain dormant in the soil seedbank (Beatley 1969, 1974, 1976). Long-lived shrubs and trees are more likely to exhibit branch-pruning, and or limited recruitment during drought (e.g. Hereford et al. 2006, Miriti et al. 2007), leading to reduced cover and biomass in drought-afflicted communities.
Non-native annual grasses (red brome [Bromus rubens], cheatgrass [Bromus tectorum] and Mediterranean grass [Schismus species]) have become naturalized throughout the Mojave Desert over the past century (Rickard and Beatley 1965, D'Antonio and Vitousek 1992, Brooks 1999, Reid et al. 2006, Norton et al. 2007). Annual grass cover and production is directly related to winter precipitation (Beatley 1969, Brooks and Berry 2006, Hereford et al. 2006), and several years of drought may reduce the abundance of non-native annuals in the soil sandbank (Minnich 2003). Non-native annual cover and biomass is highest on sandy soils (Rao et al. 2010), because of the higher availability of water in these soils in arid regions (Noy-Meir 1973, Austin et al. 2004). Clay-rich or rocky soils are less susceptible to high biomass loads of non-native annuals, but density of these species may still be significant, which can negatively impact diversity and abundance of native annuals (DeFalco et al. 2003, Allen et al. 2009)
Invasion by non-native annual grasses has increased the flammability of Mojave Desert vegetation communities by providing a continuous fine fuel layer between widely spaced shrubs (Brown and Minnich 1986, Brooks 1999, Brooks et al. 2004, Rao and Allen 2010, Rao et al. 2010). After fire, these communities appear to be more susceptible to invasion by exotic grasses, leading to a grass-fire cycle (D'Antonio and Vitousek 1992). Because of the high densities typical of blackbrush-dominated communities, these communities are flammable even without the presence of fine fuels (Brooks et al. 2007). However, where blackbrush is co-dominant with other shrubs, such as in this ecological site, densities are typically lower, which reduces flammability unless fine fuels are present in intershrub spaces.
State and transition model
Figure 4. R030XB221CA
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Ecosystem states
State 2 submodel, plant communities
State 3 submodel, plant communities
State 1
Historic State
State 1 represents the historic range of variability for this ecological site. This state no longer exists due to the ubiquitous naturalization of non-native species in the Mojave Desert. Periodic drought and rare fire were the natural disturbances influencing this ecological site. Fire would have been a very rare occurrence due to the lack of a continuous fine fuel layer between shrubs (Brown and Minnich 1986, Brooks et al. 2007). Data for this State does not exist, but dynamics and composition would have been similar to State 2, except with only native species present. See State 2 narrative for more detailed information.
State 2
Reference State
State 2 represents the current range of variability for this site. Non-native annuals, including red brome and red-stem stork’s bill are naturalized in this plant community. Their abundance varies with precipitation, but they are at least sparsely present (as current year’s growth or present in the soil seedbank).
Community 2.1
Reference plant community
Figure 5. Community Phase 2.1
Figure 6. Comunity Phase 2.1
The reference plant community is co-dominated by blackbrush, and burrobush, and secondary shrub diversity is high. Hall’s shrubby spurge, Mojave yucca (Yucca schidigera), Parry’s beargrass, Nevada jointfir (Ephedra nevadensis), and eastern Mojave buckwheat (Eriogonum fasciculatum) are important seconday shrubs. Desertsenna (Senna armata), Mojave indigobush (Psorothamnus arborescens), lotebush, mouse’s eye, waterjacket (Lycium andersonii), desert polygala (Polygala acanthoclada), and Acton’s brittlebush (Encelia actonii) may be present. A high diversity of cactus species is typically present, including branched pencil cholla (Cylindropuntia ramosissima), golden cholla (Cylindropuntia echinocarpa), beavertail pricklypear (Opuntia basilaris), cushion foxtail cactus (Escobaria alversonii), cottontop cactus (Echinocactus polycephalus), and Engelmann’s hedgehog cactus (Echinocerus engelmannii). The subshrubs Mojave aster (Xylorhiza tortifolia), brownplume wirelettuce (Stephanomeria pauciflora), narrowleaf bedstraw (Galium angustifolium), wishbone bush (Mirabilis laevis var. villosa), and desert pepperweed (Lepidium fremontii) are typically present. The annual forb component of this ecological site has low production, but common species that may be present include pygmy poppy (Escholzia minutiflora), spotted hindseed (Eucrypta chrysanthemifolia), cryptantha (Cryptantha spp.), and Mojave desertparsley (Lomatium mohavense). Red brome and red-stem stork’s bill are typically present at low levels.
Figure 7. 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) |
|---|---|---|---|
| Shrub/Vine | 195 | 291 | 387 |
| Forb | 0 | 5 | 10 |
| Grass/Grasslike | 0 | 1 | 5 |
| Total | 195 | 297 | 402 |
Community 2.2
Drought response
This community phase is characterized by a decline in cover and production due to branch-pruning of long-lived shrubs (including blackbrush, Hall’s shrubby spurge, Nevada jointfir, and Mojave yucca), and mortality of short-lived shrubs, including burrobush, eastern Mojave buckwheat, Acton’s brittlebush, desertsenna, and subshrubs. A long-term monitoring study in the reference plant community found long-periods of stability under average conditions and moderate drought, but high rates of mortality resulting from only one year of extreme drought. Following severe drought in 2002, burrobush suffered 68% mortality, Hall’s shrubby spurge 58%, and short-lived shrubs and subshrubs up to 100% mortality (Miriti et al. 2007). The increase in bare ground that occurs during drought increases the susceptibility of this site to erosion.
Community 2.3
Fire regeneration community
This community phase is characterized by the loss of blackbrush and mortality of cactus species. Initially the post-burn community is dominated by subshrubs and annuals that are quick to colonize from the seedbank or from off-site seed dispersal, and that exhibit rapid growth. With time, species capable of resprouting after fire become more important, including Mojave yucca, Nevada ephedra, waterjacket, lotebush, and Parry’s beargrass. Shrubs capable of quickly colonizing after fire include burrobush, eastern Mojave buckwheat, and Acton’s brittlebush. With very long periods of time with no disturbance (e.g. 100 years), blackbrush re-colonizes, and very gradually replaces shorter-lived species. This community is an at-risk phase. The increased cover and biomass of non-native annual grasses increases the likelihood of repeat burning. If the fire return interval is less than 100 years, this community is very likely to transition to State 3. Reduction in shrub cover increases bare ground and increases the risk of erosion.
Pathway 2.1a
Community 2.1 to 2.2
This pathway occurs with severe or prolonged drought.
Pathway 2.1b
Community 2.1 to 2.3
This pathway occurs with moderate to severe fire.
Pathway 2.2a
Community 2.2 to 2.1
This pathway occurs with a return to average or above average climatic conditions.
Pathway 2.2b
Community 2.2 to 2.3
This pathway occurs with moderate to severe fire. Although live annuals are largely absent from Community Phase 2.2, standing annual biomass in drought years immediately following a period of heavy precipitation poses a risk for fire.
Pathway 2.3a
Community 2.3 to 2.1
This pathway occurs with a long period of time without disturbance (> 100 years).
State 3
Burned, blackbrush lost
This state is characterized by the loss of blackbrush from the plant community due to severe or recurrent fire. Data does not exist for this state, and community phase composition is based on literature review. The dynamics for this state are assumed to be similar to that described in State 2, except that blackbrush is no longer part of the plant community.
Community 3.1
Blackbrush lost Reference plant community
The reference plant community for this state is dominated by burrobush. Mojave yucca, Nevada ephedra, and eastern Mojave buckwheat are important secondary species. Other shrub species, subshrubs and annuals are likely to remain as described in Community phase 2.1.
Community 3.2
Drought response
This community phase is characterized by a decline in cover and production due to branch-pruning of long-lived shrubs, and mortality of shorter-lived perennials (including eastern Mojave buckwheat, burrobrush, Cooper’s goldenbush, and desert needlegrass), and lack of emergence of annual forbs and grasses. See narrative for Community Phase 2.2 for more information.
Community 3.3
Fire regeneration community
This community phase is as described for Community phase 2.3, except that blackbrush does not return to this plant community. This phase is not at risk for transitioning to an altered state, since the species that dominate the reference plant community are resilient to fire, and given the low potential high biomass of non-native annuals in this site.
Pathway 3.1a
Community 3.1 to 3.2
This pathway occurs in response to prolonged or severe drought.
Pathway 3.1b
Community 3.1 to 3.3
This pathway occurs in response to moderate or severe fire.
Pathway 3.2a
Community 3.2 to 3.1
This pathway occurs with time and a return to average or above average precipitation.
Pathway 3.2b
Community 3.2 to 3.3
This pathway occurs with moderate to severe fire. Although live annuals are largely absent from Community Phase 3.2, standing annual biomass in drought years immediately following a period of heavy precipitation poses a risk for fire.
Pathway 3.3a
Community 3.3 to 3.1
This pathway occurs with time without fire.
Transition 1
State 1 to 2
This transition occurred with the naturalization of non-native species in this ecological site. Non-native species were introduced with settlement of the Mojave Desert region in the 1860s. Post-settlement cattle and sheep grazing, as well as dryland farming, helped to spread and facilitate their establishment (Brooks and Pyke 2000, Brooks et al. 2007).
Transition 2
State 2 to 3
This transition occurs with extensive, severe fire when blackbrush seed sources are not available to colonize burned areas, or with recurrent fire.
Restoration pathway 1
State 3 to 2
Restoration of arid desert communities severely altered by repeat fire at the landscape scale is very difficult (Allen 1993). Reducing invasion of non-native grasses that increase after fire may help promote native plant recovery, and reduce the probability of repeat burning (Fuhrmann et al. 2009, Matchett et al. 2009, Steers and Allen 2010); however, accomplishing this at a landscape scale, for a time period long enough to be effective, has not yet been accomplished. In small-scale trials, Fusilade, a grass-specific herbicide, was successful in reducing invasive grasses in burned creosote bush communities in the Colorado Desert in the initial three years after fire (Steers and Allen 2010). The long-term efficacy of such treatments on a landscape scale, and non-target effects have not yet been determined. The pre-emergent herbicide Plateau was applied in conjunction with aerial seeding of natives after fire in Zion National Park (Fuhrmann et al. 2009, Matchett et al. 2009). Initial results indicate that autumn application of Plateau after fire is most effective for reducing cheatgrass (Bromus tectorum), but longer-term monitoring is needed to evaluate long-term and non-target effects. In addition to controlling invasive species, active recovery of native vegetation may be attempted. Methods may include seeding of early native colonizers such as desert globemallow, burrobrush, threeawns (Aristida spp.), and desert marigold (e.g. Abella et al. 2009, Abella et al. 2012). Increased native cover may help to reduce non-native plant invasion, helps to stabilize soils, provides a source of food and cover for wildlife, including desert tortoise (Gopherus agassizii), and provides microsites that facilitate blackbrush establishment. However, the amount of seed required for success is often prohibitive. Large-scale planting of both early colonizers and community dominants tends to be more successful in terms of plant survival, especially if outplants receive supplemental watering during the first two years (Allen 1993). Blackbrush is difficult to cultivate for outplanting due to susceptibility to fungal pathogens in the greenhouse environment.
Additional community tables
Table 6. Community 2.1 plant community composition
| Group | Common name | Symbol | Scientific name | Annual production (lb/acre) | Foliar cover (%) | |
|---|---|---|---|---|---|---|
|
Shrub/Vine
|
||||||
| 1 | Native shrubs | 195–387 | ||||
| blackbrush | CORA | Coleogyne ramosissima | 90–180 | 2–10 | ||
| burrobush | AMDU2 | Ambrosia dumosa | 50–160 | 1–10 | ||
| Mojave indigobush | PSAR4 | Psorothamnus arborescens | 0–35 | 0–1 | ||
| Eastern Mojave buckwheat | ERFA2 | Eriogonum fasciculatum | 2–30 | 0–1 | ||
| California juniper | JUCA7 | Juniperus californica | 0–25 | 0–4 | ||
| desertsenna | SEAR8 | Senna armata | 0–25 | 0–1 | ||
| Mojave yucca | YUSC2 | Yucca schidigera | 0–21 | 1–5 | ||
| Bigelow's nolina | NOBI | Nolina bigelovii | 2–20 | 0–2 | ||
| Nevada jointfir | EPNE | Ephedra nevadensis | 5–15 | 1–2 | ||
| branched pencil cholla | CYRA9 | Cylindropuntia ramosissima | 1–15 | 0–1 | ||
| Hall's shrubby-spurge | TEHA | Tetracoccus hallii | 3–10 | 1–2 | ||
| Wiggins' cholla | CYEC3 | Cylindropuntia echinocarpa | 1–8 | 0–1 | ||
| Acton's brittlebush | ENAC | Encelia actonii | 0–5 | 0–1 | ||
| lotebush | ZIOB | Ziziphus obtusifolia | 0–5 | 0–1 | ||
| Parry's wirelettuce | STPA3 | Stephanomeria parryi | 0–5 | 0–1 | ||
| desert polygala | POAC2 | Polygala acanthoclada | 0–5 | 0–1 | ||
| water jacket | LYAN | Lycium andersonii | 0–3 | 0–1 | ||
| beavertail pricklypear | OPBA2 | Opuntia basilaris | 0–3 | 0–1 | ||
| Mojave woodyaster | XYTO2 | Xylorhiza tortifolia | 0–1 | 0–3 | ||
| cushion foxtail cactus | ESAL2 | Escobaria alversonii | 0–1 | 0–1 | ||
| Engelmann's hedgehog cactus | ECEN | Echinocereus engelmannii | 0–1 | 0–1 | ||
| cottontop cactus | ECPO2 | Echinocactus polycephalus | 0–1 | 0–1 | ||
| mouse's eye | BEMY | Bernardia myricifolia | 0–1 | 0–1 | ||
|
Forb
|
||||||
| 2 | Native forbs | 0–10 | ||||
| desert pepperweed | LEFR2 | Lepidium fremontii | 0–9 | 0–1 | ||
| Mojave desertparsley | LOMO | Lomatium mohavense | 0–1 | 0–1 | ||
| wishbone-bush | MILAV | Mirabilis laevis var. villosa | 0–1 | 0–1 | ||
| cryptantha | CRYPT | Cryptantha | 0–1 | 0–1 | ||
| flatcrown buckwheat | ERDE6 | Eriogonum deflexum | 0–1 | 0–1 | ||
| pygmy poppy | ESMI | Eschscholzia minutiflora | 0–1 | 0–1 | ||
| spotted hideseed | EUCH | Eucrypta chrysanthemifolia | 0–1 | 0–1 | ||
| narrowleaf bedstraw | GAAN2 | Galium angustifolium | 0–1 | 0–1 | ||
| 3 | Non-native annual forbs | 0–1 | ||||
| redstem stork's bill | ERCI6 | Erodium cicutarium | 0–1 | 0–1 | ||
|
Grass/Grasslike
|
||||||
| 4 | Non-native annual grasses | 0–1 | ||||
| red brome | BRRU2 | Bromus rubens | 0–1 | 0–1 | ||
Interpretations
Animal community
A diverse assemblage of reptiles and mammals are likely to be found in this site. These may include (based on habitat preferences):
Lizards:
Mojave Desert tortoise (Gopherus agassizii agassizii)
Desert banded Gecko (Coleonyx variegatus variegatus)
Northern desert iguana (Dipsosaurus dorsalis dorsalis)
Long-nosed leapard lizard (Gambelia wislizenii wislizenii)
Western chuckwalla (Sauromalus ater obesus)
Mojave zebra-tailed lizard (Callisaurus draconoides rhodostictus)
Southern desert horned lizard (Phrynosoma platyrhinos calidiarum)
Western brush lizard (Urosaurus graciosus graciosus)
Desert side-blotched lizard (Uta stansburiana stejnegeri)
Great basin whiptail (Aspidoscelis tigris tigris)
Snakes:
Desert glossy snake (Arizona occidentalis eburnata)
Mojave shovel-nosed snake (Chionactis occipitalis occipitalis)
California kingsnake (Lampropeltis getula californae)
Red coachwhip (Masticophis flagellum piceus)
Western leaf-nosed snake (Phyllorynchus decurtatus perkinsi)
Sonoran gopher snake (Pituophis catenifer affinis)
Western long-nosed snake (Rhinocheilus lecontei lecontei)
Desert patch-nosed snake (Salvadora hexalepis hexalepis)
Smith's black-headed snake (Tantilla hobartsmithi)
Western diamondback snake (Crotalus atrox)
Mojave Desert sidewinder (Crotalus cerastes cerastes)
Colorado Desert sidewinder (Crotalus cerastes laterorepens)
The following mammals are likely to occur in this ecological site:
American badger (Taxidea taxus berlandieri)
California desert bat (Myotis californicus stephensi)
Western pipistrelle (Pipistrellus hesperus hesperus)
Desert big brown bat (Eptesicus fuscus pallidus)
Pallid bat (Antrozous pallidus minor)
Desert coyote (Canis macrotis arsipus)
Desert kit fox (Vulpes macrotis arsipus)
Southern Desert cottontail (Sylvilagus audobonii arizonae)
Desert blacktail jackrabbit (Lepus californicus deserticola)
Whitetail antelope squirrel (Ammospermphilus leucurus leucurus)
Mojave roundtail ground squirrel (Spermophilus tereticaudus tereticaudus)
Mojave pocket gopher (Thomomys bottae mojavensis)
Coachella pocket gopher (Thomomys bottae rupestris)
Eastern spiny pocket mouse (Peroganthus spinatus spinatus)
Pallid (San Diego) pocket mouse (Chaetodipus fallax pallidus)
Mojave little pocket mouse (Perognathus longimembris longimembris)
Merriam's kangaroo rat (Dipodomys merriami merriami)
Desert kangaroo rat (Dipodomys deserti)
Desert wood rat (Neotoma fuscipes simplex)
Sonoran deer mouse (Peromyscus maniculatus sonoriensis)
Desert grasshopper mouse (Onychomys torridus pulcher)
Desert shrew (Notiosorex crawfordi crawfordi
Recreational uses
This site may be used for botanizing, wildflower viewing, and aesthetic enjoyment. The plant community represents an interesting assemblage of Mojave and Sonoran Desert species that come together at this transitional area.
Other products
The Kawaiisu used a decoction of blackbrush bark for treating gonorrhea Drug (http://herb.umd.umich.edu/herb/search.pl?searchstring=Coleogyne+ramosissima.
The Havasupai used blackbrush as source of fodder when grass was not available (http://herb.umd.umich.edu/herb/search.pl?searchstring=Coleogyne+ramosissima).
Supporting information
Inventory data references
The following NRCS vegetation plots were used to describe this ecological site:
Community Phase 2.1:
POWA63 (Type location)
POWA18
POWA24
Type locality
| Location 1: Riverside County, CA | |
|---|---|
| UTM zone | N |
| UTM northing | 3734940 |
| UTM easting | 609080 |
| General legal description | The type location is approximately 500 feet east-northeast from the Cottonwood Visitor's Center in Joshua Tree National Park. |
Other references
Abella, S. R., J. L. Gunn, M. L. Daniels, J. D. Springer, and S. E. Nyoka. 2009. Using a diverse seed mix to establish native plants on a Sonoran Desert burn. Native Plants Journal 10:21-31.
Abella, S. R., E. C. Engel, C. L. Lund, and J. E. Spencer. 2009. Early post-fire establishment on a Mojave Desert burn. Madroño 56:137-148.
Abella, S. R., D. J. Craig, S. D. Smith, and A. C. Newton. 2012. Identifying native vegetation for reducing exotic species during the restoration of desert ecossytems. Restoration Ecology.
Allen, E. B. 1993. Restoration ecology: limits and possibilities in arid and semiarid lands. Pages 7-15 in Wildland shrub and arid land restoration symposium. U.S. Department of Agriculture, Forest Service, Intermountain Research Station, Las Vegas, NV.
Allen, E. B., L. E. Rao, R. J. Steers, A. Bytnerowicz, and M. E. Fenn. 2009. Impacts of atmospheric nitrogen deposition on vegetation and soils at Joshua Tree National Park. Pages 78-100 in R. H. Webb, L. F. Fenstermaker, J. S. Heaton, D. L. Hughson, E. V. McDonald, and D. M. Miller, editors. The Mojave Desert. University of Nevada Press, Reno, Nevada.
Austin, A. T., L. Yahdjian, J. M. Stark, J. Belnap, A. Porporato, U. Norton, D. A. Ravetta, and S. M. Scheaeffer. 2004. Water pulses and biogeochemical cycles in arid and semiarid ecosystems. Oecologia 141:221-235.
Beatley, J. C. 1969. Dependence of desert rodents on winter annuals and precipitation. Ecology 50:721-724.
Beatley, J. C. 1974. Effects of rainfall and temperature on the distribution and behavior of Larrea tridentata (Creosote-bush) in the Mojave Desert of Nevada. Ecology 55:245-261.
Beatley, J. C. 1976. Rainfall and fluctuating plant populations in relation to distributions and numbers of desert rodents in southern Nevada. Oecologia 24:21-42.
Bowers, J. E. 2005. Effects of drought on shrub survival and longevity in the northern Sonoran Desert. Journal of the Torrey Botanical Society 132:421-431.
Brooks, M. L. 1999. Habitat invasibility and dominance by alien annual plants in the western Mojave Desert. Biological Invasions 1:325-337.
Brooks, M. L. and K. H. Berry. 2006. Dominance and environmental correlates of alien annual plants in the Mojave Desert, USA. Journal of Arid Environments 67:100-124.
Brooks, M. L., C. M. D'Antonio, D. M. Richardson, J. B. Grace, J. E. Keeley, J. M. DiTomaso, R. J. Hobbs, M. Pellant, and D. Pyke. 2004. Effects of invasive alien plants on fire regimes. Bioscience 54:677-689.
Brooks, M. L., T. C. Esque, and T. Duck. 2007. Creosotebush, blackbrush, and interior chaparral shrublands. RMRS-GTR-202.
Brooks, M. L. and J. R. Matchett. 2003. Plant community patterns in unburned and burned blackbrush (Coleogyne ramosissima Torr.) shrublands in the Mojave Desert. Western North American Naturalist 63:283-298.
Brooks, M. L. and D. A. Pyke. 2000. Invasive plants and fire in the deserts of North America. Pages 1-14 in Fire conference 2000: the first national congress on fire ecology, prevention, and management. Tall Timbers Research Station, Tallahassee, FL.
Brown, D. E. and R. A. Minnich. 1986. Fire and Changes in Creosote Bush Scrub of the Western Sonoran Desert, California. American Midland Naturalist 116:411-422.
Cole, R. H. and R. H. Webb. 1985. Late Holocene Vegetation Changes in Greenwater Valley, Mojave Desert, California. Quaternary Research 23:227-235.
D'Antonio, C. M. and P. M. Vitousek. 1992. Biological invasions by exotic grasses, the grass/fire cycle, and global change. Annual Review of Ecology and Systematics 23:63-87.
DeFalco, L. A., D. R. Bryla, V. Smith-Longozo, and R. S. Nowak. 2003. Are Mojave Desert annual species equal? Resource acquisition and allocation for the invasive grass Bromus madritensis subsp. rubens (Poaceae) and two native species. American Journal of Botany 90:1045-1053.
Fuhrmann, K., K. Weber, and C. Decker. 2009. Restoring burned areas at Zion National Park (Utah). Restoration Ecology 27:132-133.
Hereford, R., R. H. Webb, and C. I. Longpre. 2006. Precipitation history and ecosystem response to multidecadal precipitation variability in the Mojave Desert region, 1893-2001. Journal of Arid Environments 67:13-34.
Lei, S. A. 1997. Variation in germination response to temperature and water availability in blackbrush (Coleogyne ramosissima) and its ecological significance. Great Basin Naturalist 57:172-177.
Matchett, J. R., A. O'Neill, M. Brooks, C. Decker, J. Vollmer, and C. Deuser. 2009. Reducing fine fuel loads, controlling invasive annual grasses, and manipulating vegetation composition in Zion Canyon, Utah. Joint Fire Science Program, El Portal, California.
Minnich, R. A. 2003. Fire and dynamics of temperature desert woodlands in Joshua Tree National Park. Contract, Joshua Tree National Park.
Miriti, M. N., S. Rodriguez-Buritica, S. J. Wright, and H. F. Howe. 2007. Episodic death across species of desert shrubs. Ecology 88:32-36.
Norton, J. B., T. A. Monaco, and U. Norton. 2007. Mediterranean annual grasses in western North America: kids in a candy store. Plant Soil 298:1-5.
Noy-Meir, I. 1973. Desert ecosystems: environment and producers. Annual Review of Ecology and Systematics 4:25-51.
Pendleton, B. K. and S. E. Meyer. 2004. Habitat-correlated variation in blackbrush (Coleogyne ramosissima: Rosaceae) seed germination response. Journal of Arid Environments 59:229-243.
Pendleton, B. K., S. E. Meyer, and R. L. Pendleton. 1995. Blackbrush biology: insights after three years of a long-term study. Pages 223-228 in Wildland shrub and arid land restoration symposium. U.S. Department of Agriculture, Forest Service, Intermountain Research Station, Las Vegas, NV.
Rao, L. E. and E. B. Allen. 2010. Combined effects of precipitation and nitrogen deposition on native and invasive winter annual production in California deserts. Oecologia 162:1035-1046.
Rao, L. E., E. B. Allen, and T. M. Meixner. 2010. Risk-based determination of critical nitrogen deposition loads for fire spread in southern California deserts. Ecological Applications 20:1320-1335.
Reid, C. R., S. Goodrich, and J. E. Bowns. 2006. Cheatgrass and red brome: history and biology of two invaders. Pages 27-32 in Shrublands under fire: disturbance and recovery in a changing world. U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station, Cedar City, Utah.
Rickard, W. H. and J. C. Beatley. 1965. Canopy-coverage of the desert shrub vegetation mosaic of the Nevada test site. Ecology 46:524-529.
Steers, R. J. and E. B. Allen. 2010. Post-fire control of invasive plants promotes native recovery in a burned desert shrubland. Restoration Ecology 18:334-343.
Vamstad, M. S. 2009. Effects of fire on vegetation and small mammal communities in a Mojave Desert Joshua tree woodland. M.S. University of California, Riverside, Riverside, Ca.
Webb, R. H., M. B. Muroy, T. C. Esque, D. E. Boyer, L. A. DeFalco, D. F. Haines, D. Oldershaw, S. J. Scoles, K. A. Thomas, J. B. Blainey, and P. A. Medica. 2003. Perennial vegetation data from permanent plots on the Nevada Test Site, Nye County, Nevada. U.S. Geological Society, Tucson, AZ.
Contributors
Alice Miller
Marchel M. Munnecke
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 | |
| Approved by | |
| Approval date | |
| Composition (Indicators 10 and 12) based on | Annual Production |
Indicators
-
Number and extent of rills:
-
Presence of water flow patterns:
-
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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