Tarbush at Big Bend National Park, Texas.
Photo courtesy of Melody Lytle, Lady Bird Johnson Wildflower Center Native Plant Information Network.
AUTHORSHIP AND CITATION:
Innes, Robin J. 2010. Flourensia cernua. In: Fire Effects Information System, [Online]. U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station, Fire Sciences Laboratory (Producer). Available: http://www.fs.fed.us/database/feis/ .
NRCS PLANT CODE :
The common name "blackbrush" is frequently used to denote Flourensia cernua (e.g., [23,24,30,40,109]), but this common name is reserved in FEIS for Coleogyne ramosissima.
The scientific name of tarbush is Flourensia cernua DC (Asteraceae) [39,68].
Tarbush occurs primarily on plains and mesas throughout the Chihuahuan Desert, the second largest desert in North America. The Chihuahuan Desert occurs in southeastern Arizona, southern New Mexico, southwestern Texas, and Mexico [10,65,118]. In Mexico, tarbush occurs in the states of Sonora, Chihuahua, Coahuila, Durango, San Luis Potosi, and Zacatecas . One publication stated that tarbush occurs in California , but this appears to be erroneous, as tarbush is not included in California floras. NatureServe provides a distributional map of tarbush.
HABITAT TYPES AND PLANT COMMUNITIES:
Tarbush occurs in desert scrub and desert grassland habitats and their intergradations (e.g., [10,14,29,42,46,65,78,106,118,123]). In part a result of historical overgrazing, tarbush has replaced grama (Bouteloua spp.) and tobosa (Pleuraphis mutica) grasses as dominants in many desert grasslands throughout its distribution. Thus, tarbush is often considered "invasive" in desert grasslands [11,28,49,56,111]. See Other Management Considerations for more information on this topic.
Tarbush primarily occurs in the Chihuahuan Desert. Chihuahuan Desert scrub is the predominant plant community throughout the Chihuahuan Desert, covering about 70% of its area [55,86]. Tarbush is considered a characteristic or indicator plant species of Chihuahuan Desert scrub [10,29,65,118]. Chihuahuan Desert scrub is dominated primarily by tarbush, creosotebush (Larrea tridentata), and viscid acacia (Acacia neovernicosa) [104,130]. Because secondary shrubs and cacti formed <10% of stands, Shreve  described areas of Chihuahuan Desert scrub as "uniform and monotonous".
Within Chihuahuan Desert scrub, tarbush is most commonly associated with creosotebush. Tarbush may be dominant, codominant, or subdominant to creosotebush (e.g., [19,46,55,58,84,104,121,132,137,155]). In the Rio Grande Valley, New Mexico, 96% of habitats with tarbush also had creosotebush with varying degrees of dominance. The authors found that the 2 species were associated more often than would be expected from random mixing (P=0.01) . The abundance and distribution of tarbush in relation to creosotebush depend partly upon site conditions. Creosotebush-tarbush habitat is common on the plains below the desert mountains in the Chihuahuan Desert with decreasing tarbush cover and increasing creosotebush cover in the warmest, most arid areas and increasing tarbush and decreasing creosotebush cover in deep soils and along minor drainages [55,58]. For more information on this topic, see Site Characteristics.
Tarbush also occurs in desert scrub communities dominated by acacia (e.g., whitethorn acacia (Acacia constricta) [60,121,155], viscid acacia [104,105,137], catclaw acacia (A. greggii) ), honey mesquite (Prosopis glandulosa) [11,22,49], Berlandier wolfberry (Lycium berlandieri) [52,108,121], mariola (Parthenium incanum) [105,137,142], Wright's beebrush (Aloysia wrightii), littleleaf sumac (Rhus microphylla) , broom snakeweed (Gutierrezia sarothrae) [4,149], winterfat (Krascheninnikovia lanata) , or smooth-leaf sotol (Dasylirion leiophyllum) . Throughout the Trans-Pecos region, tarbush occurred in the viscid acacia shrubland alliance on lower foothills of mountains, mesas, and piedmont hills and ridges at 4,200 to 6,300 feet (1,280-1,930 m) . Tarbush occurred in a cattle-grazed broom snakeweed-tarbush-burroweed (Isocoma tenuisecta) community in the San Simon Valley, southeastern Arizona . Tarbush-tobosa and tarbush-burrograss associations occurred on gravelly clay loam , and the tarbush-winterfat-Berlandier's wolfberry community occurred on fine loam  at the Jornada Experimental Range, south-central New Mexico. On the east-facing slope of Bishop's Cap Peak at 4,800 feet (1,465 m) in Dona Ana County, New Mexico, tarbush occurred in Berlandier wolfberry-creosotebush communities on ledges below limestone cliffs . Tarbush occurred "in abundance" in smooth-leaf sotol grassland on gravelly slopes of the Grapevine Hills in Big Bend National Park, Texas .
Tarbush commonly occurs scattered throughout desert grassland and in the desert grassland-desert scrub ecotone . Tarbush occurs most commonly in and adjacent to desert grasslands dominated by grama, tobosa, and burrograss (Scleropogon brevifolius) (e.g., [10,13,21,32,41,43,49,67,110,155]). Tarbush occurred in a clay bottomland site in tobosa grassland at the Jornada Experimental Range, New Mexico . Tarbush-tobosa-burrograss communities occurred as bands of vegetation on low slopes (<2% slope) of the watersheds of the Doña Ana Mountains located between unvegetated bands of soil . In gypsiferous soil in New Mexico, scattered tarbush occurred in the gyp dropseed (Sporobolus nealleyi) herbaceous alliance . On the Stockton Plateau in western Texas, tarbush occurred in banded vegetation as scattered individuals in burrograss and purple threeawn (Aristida purpurea) communities . Also in western Texas, tarbush occurred in the grama-muhly (Muhlenbergia spp.)-purple threeawn association . In Big Bend National Park, tarbush occurred in black grama-red grama-China grama (Bouteloua eriopoda-B. trifida-B. ramosa) grasslands . In intermittently flooded depressions and floodplains throughout the Trans-Pecos region, tarbush occurred as scattered individuals in the tobosa intermittently flooded herbaceous alliance .
The only mention of tarbush occurring in pinyon-juniper (Pinus spp.-Juniperus spp.) woodlands was on the Gila National Forest in southwestern New Mexico .
Vegetation classifications describing plant communities where tarbush is a dominant species follow:Arizona:
GENERAL BOTANICAL CHARACTERISTICS:
Form and architecture: Tarbush is a native perennial C3 shrub . It is many branched and densely leafy [69,118,135,153]. Its growth form may be erect or procumbent [135,153]. Tarbush plants do not have trunks; instead, the branches run obliquely from the base . It grows from <1 foot (0.3 m) to >7 feet (2 m) tall [75,118,131,153].
Tarbush in the Burro Mountains, Engineer Canyon, Gila National Forest.
Photo courtesy of Russ Kleinman and Richard Felger.
Leaves: The thick leaves of tarbush are alternate, simple, and elliptical [118,153]. Tarbush leaves may be up to 1 inch (2.5 cm) long [75,118]. Most researchers describe tarbush leaves as winter deciduous (e.g., [26,45,66,113,152]). Near Las Cruces, New Mexico, tarbush was described as "partially" winter deciduous because some tarbush plants along arroyos (ephemeral stream beds) held some leaves throughout the winter .
Reproductive structures: Tarbush's composite flower heads are small, solitary, and inconspicuous [135,153]. The yellow-disked flower heads lack ray flowers and are pendant . Each flower head has up to 20 flowers [135,153]. The flowers are hermaphroditic . The fruits are one-seeded achenes that are flattened, hairy, and about 0.3 inch (6 mm) long [75,89,118,131,153].
Tarbush flowers, achenes, leaves, and stems are highly resinous [135,146]. Tarbush produces a characteristic tar-like odor [118,135] due to the presence of secondary compounds .
Roots: Tarbush has tap roots [52,89]. It is able to exploit both shallow and deep soil moisture. Tarbush is often described as shallow rooted (, Muldavin 1998 cited in ) because >75% of adult tarbush roots are located within the upper 16 inches (40 cm) of soil . Tarbush roots spread horizontally up to 13 feet (4 m) [21,52]. As a result, tarbush plants depend mostly on water from the upper soil layers [21,101], which is recharged by common, small rainfall events . Thus, small rainfall events are likely critical to the establishment and survival of tarbush . In a field experiment in Durango, Mexico, tarbush responded to increased water availability in the upper soil layers by significantly increasing stem growth (P<0.05) . A small number of tarbush roots are deep (up to >16 feet (5 m)) . These roots can access water from horizons that recharge infrequently and may sustain individual plants during lengthy droughts [12,52].
Tarbush roots may be deepest in soils with abundant run-off water  or in sparsely vegetated areas . In Durango, Mexico, tarbush seedlings grown in unvegetated areas had significantly deeper root systems than seedlings grown under herbaceous cover (P<0.05) . Tarbush seedlings can develop root biomass rapidly . The deepest roots reported for a 1-year-old tarbush seedling were 16.1 inches (41 cm) for a 2-inch (5 cm) tall shoot in Durango, Mexico .
Stand and age-class structure: Communities with tarbush are usually open, with scattered shrubs and herbs and extensive bare interspaces, but vegetation may vary from very open to moderately dense (e.g., [10,14,55,65,89,121]). Tarbush may be locally or generally abundant [63,69]. It may occur in very open stands of widely-spaced individuals [11,78,106] or in dense clumps [30,75,78,89]. In Brewster County, Texas, the tobosa-tarbush association was described as arid and open with tarbush and other shrubs usually spaced 2 to 3 feet (0.6-0.9 m) apart . In Hidalgo County, New Mexico, the nearest-neighbor distance between tarbush plants averaged 0.79 feet (0.24 m) in dense tarbush-dominated stands (3,800 tarbush plants/ha) . Although tarbush commonly occurs with other shrubs (e.g., [41,82]), it may occur in pure or nearly pure stands [28,49,107,125,130]. Tarbush tends to occur in pure stands in areas with clay and silt soils  and along bottomlands . Studies reported tarbush cover ranging from 5% to 45% in tarbush-dominated sites [36,51,67,89,99,101,108,111,129]. See Fuels for more information on tarbush stand structure and composition.
Limited information is available on tarbush's age class structure as of this writing (2010). Tarbush was described as long lived [142,147], although a life span was not provided. In a photo taken of a tarbush-dominated stand in 1937 and again in 2002 at the Jornada Experimental Range, some individual tarbush plants were apparently still present after 63 years, indicating that tarbush may live at least that long . Tarbush plant age (number of growth rings) and stem diameter are positively correlated (R²=0.89, P<0.001). Based on this relationship, a 10-year-old juvenile tarbush plant would have a stem diameter of approximately 0.8 inch (2 cm). High density of tarbush seedlings (<1-year-old plants) indicates tarbush may have high recruitment during some years. In Durango, Mexico, mean tarbush seedling density was 1.9 seedlings/m²; the maximum reported seedling density was 85 seedlings/m² .
Physiology: Tarbush's presence in arid environments suggests that it is highly tolerant of drought . Tarbush tolerates flooding for short periods but cannot withstand long-term standing water . Tarbush responds quickly to increased water availability by increasing photosynthesis and transpiration rates. Although tarbush inhabiting arroyos in New Mexico responded quickly to cycles of water availability, rainfall that did not increase channel flow in the arroyos did not appear sufficient to provide sustained relief from drought .
Tarbush leaf emergence occurs in spring. The timing of spring leaf emergence depends on the distribution and amount of winter and spring precipitation, but green leaves are typically present in late May or early June. In south-central New Mexico, in years with a dry winter and spring, tarbush plants reduced photosynthetic activity and produced small, scale-like leaves in May and early June. These plants shed the small leaves and produced a new set of larger leaves as moisture availability increased in summer . During a year of abundant winter and spring precipitation at the Jornada Experimental Range, the growing season began earlier than usual, in early May . Tarbush's peak growing period appears coincident with the period of maximum rainfall (see Climate). Most tarbush stem growth occurs in summer after the summer rains begin [35,134].
Tarbush generally flowers in fall at the end of the rainy season [35,89,134,147]:
|General flowering period for tarbush throughout its range|
|Arizona||southeastern Arizona||July-December |
|New Mexico||Jornada Plain, south-central New Mexico||October |
|Texas||western Texas||September-December, but usually October |
|Mexico||Mapimi Biosphere Reserve, Durango||November [89,147]|
After flowering, tarbush growth wanes and leaves senesce [35,73]. Tarbush loses most leaves after freezing temperatures occur, although some desiccated leaves may remain on the plant until the following spring (, P.W. Hyder personal observation cited in ). Near Las Cruces, New Mexico, tarbush leaves were completely senesced in December .
Tarbush fruits mature and seeds disperse in winter during the dry season [75,89].
In Durango, Mexico, tarbush produced fruit from December to February and dispersed seeds during
February and March. Tarbush seeds germinate in summer during the rainy season. In Durango,
Mexico, tarbush seeds germinated from July through August [89,147].
Pollination and breeding system: Tarbush flowers are wind pollinated (, Mauchamp 1992 cited in ). Tarbush flowers are hermaphroditic and self-incompatable . In field experiments, the production of viable seeds after selfing was low (2-4% of flowers produced a viable seed), whereas the production of viable seeds after cross-pollination was up to 20% (M. Ferrer unpublished data cited in ).
Seed production: Tarbush produces abundant seed annually [13,89]. However, the majority of tarbush seeds are inviable [37,147]. In Durango, Mexico, individual tarbush plants produced 0 to 22 viable seeds/plant from approximately 5,000 ovules per plant (Ferrer 2004 cited in ). The viability of seeds derived from outcrossing was higher than that of seeds derived from selfing (see Pollination and breeding system) . Of those seeds that were viable, the proportion of seeds that germinated was low (9%) (Ferrer 2004 cited in ). For more information on this topic, see Germination.
Precipitation, temperature, and insect herbivory may affect tarbush flowering and seed production. At the Jornada Experimental Range, tarbush did not flower during 2 years of a 3-year study due to dry conditions and extensive defoliation by leaf beetles (Zygogramma tortuosa). During a year of abundant winter and spring precipitation, however, tarbush herbage was lush and green, leaf beetle herbivory was less, and tarbush plants flowered sporadically in mid-October . In Durango, Mexico, tarbush flowered in fall regardless of water availability . Results from these studies suggest that insect herbivory in combination with dry conditions may have a greater impact on tarbush flowering than water availability alone. In Durango, Mexico, seed quality (seed size and viability) increased with higher minimum temperatures during seed formation in winter. Increased precipitation during the same period also increased seed size but to a lesser extent . Because seed quality affects germination and seedling development, between-year variation in minimum winter temperatures and, to a lesser extent, precipitation, affect tarbush population dynamics.
Seed dispersal: Past researchers reported that tarbush seeds were "relatively motile"  and dispersed by wind . However, more recent studies reported that tarbush seeds are not dispersed by wind, but are instead dispersed initially by gravity and secondarily by water [36,89].
Tarbush seeds are dispersed short distances. In Durango, Mexico, 90% of tarbush seeds fell directly under the parent plant . The most distant tarbush seedling recorded from an adult was <16 feet (5 m) away; most were <10 feet (3 m) away. Controlled experiments with tarbush seeds suggested that they may be dispersed short distances by ants . Mauchamp and others  concluded that tarbush seeds have no apparent adaptation for long distance dispersal by wind or animals.
Spread of woody plant seed by livestock has been implicated as a cause of increased shrub encroachment into desert grasslands , particularly for honey mesquite—whose seeds remain viable after passing through cattle digestive tracts . Because livestock avoid eating tarbush, including its seeds, it is unlikely that livestock disperse tarbush seeds. For more information on this topic, see Palatability and nutritional value.
Seed banking: About 2% of tarbush seeds germinated in the laboratory after 26 months of storage, suggesting that tarbush may be capable of producing a short-term seed bank . However, because tarbush apparently produces seeds most years , it likely contributes seeds to the seed bank annually and may not rely on long-term seed banks. In a review of desert seed banks, Kemp  reported that most desert shrubs and other long-lived perennial plants such as tarbush do not require seed banks because they produce seeds almost every year that can ensure the recruitment of new individuals into the population. Thus, when conditions are favorable for shrub establishment, the seed source may be primarily seeds produced during the previous season. Tarbush seems to be long lived, and desert shrubs such as tarbush may be protected against climatic uncertainly by long life rather than by a seed bank .
In a review of desert seed banks, Kemp  reported that most (80-90%) seeds in desert seed banks occur in the upper 0.8 inch (2 cm) of soil and of those, most are located in the litter or upper 0.4 inch (1 cm) of soil. Highly clumped distributions of seeds in soils are common for desert seed banks in general, in part because of a lack of extensive dispersal. When seeds are dispersed, accumulations of seeds occur in depressions where water collects, in wind shadows of obstructions, or in animal caches . Because tarbush seeds typically fall beneath parent plants and are only minimally dispersed except secondarily by water, tarbush seeds are likely to be highly clumped spatially in soil seed banks. In Durango, Mexico, in the tarbush-western honey mesquite (P. glandulosa var. torreyana)/burrograss mixed grassland vegetation type, tarbush seedlings were clearly aggregated with adults and tarbush seed density in the upper 2 inches (5 cm) of soil decreased with increased distance from the base of an adult plant :
|Density of tarbush seeds in the soil seed bank at varying distances from adult plants in Durango, Mexico |
|Distance to plant base (m)||Mean number of tarbush seeds/m²|
Tarbush seed densities in the soil seed bank were directly related to the density of adults. In habitat where tarbush was dense, mean tarbush seed densities in the seed bank in June—after seed dispersal and prior to the summer rains—were up to 153 tarbush seeds/m². Where tarbush was sparse, mean tarbush seed densities in the seed bank were up to 5.8 seeds/m². No tarbush seeds were found in habitats without tarbush. After the summer rains in August, however, no tarbush seeds were found in the soil seed bank in any habitat. The authors suggested that this indicated substantial local displacement of seeds by water flow . The authors did not report whether tarbush seeds germinated from the seed bank.
In general, granivores such as ants and small mammals substantially reduce desert seed banks by consuming and dispersing seeds . As of this writing (2010), it is unclear whether small mammals and other granivores consume or disperse tarbush seeds; however, granivores likely avoid unpalatable or toxic seeds. Thus, species such as tarbush—whose seeds are likely unpalatable—are expected to have more persistent seed banks because they are less susceptible to granivory . For more information on this topic, see Palatability and nutritional value.
Germination: Tarbush has extremely low germination rates (<10%) compared with the average recorded for arid-land shrubs of the family Asteraceae (, Mauchamp 1992 cited in , Ferrer 2004 cited in ). Maximum germination rate of tarbush seeds reported under the best laboratory conditions was 39% .
Tarbush seed germination peaks during the summer rainy season. In the laboratory, tarbush seed germination increased when seeds were more than 3 months old, peaked for seeds 5 and 8 months old, and decreased for older seeds (14-26 months old). The peak in tarbush seed germination corresponded with the peak of the summer rainy season, suggesting that percent germination of tarbush seeds is low immediately after dispersal in winter and increases after cold winter temperatures and summer rains. Constant moisture increased tarbush seed germination in the laboratory, suggesting that tarbush seeds might have seed quiescence, where seeds only germinate when soil moisture has increased after the onset of the rainy season. In the laboratory, tarbush seed germination was inhibited by a low ratio of red:far-red light, similar to that which occurs under dense canopies, suggesting that tarbush seed germination is inhibited in areas with a dense canopy or litter cover .
Seedling establishment and plant growth: Tarbush reportedly grows at a slow rate [11,13]. Mauchamp and others  defined tarbush seedlings as <1-year-old plants with stems <0.1 inch (2 mm) in diameter, and juveniles as 1- to 10-year-old, nonflowering plants, <20 inches (50 cm) tall with stem diameters between 0.1 to 0.8 inch (2-20 mm) .
Tarbush apparently reaches its best growth in full sun. In Durango, Mexico, tarbush seedlings growing in full sun were significantly larger than shaded seedlings (P<0.05 for all variables). Tarbush seedlings emerged in shaded and unshaded sites, but as the dry season progressed, shaded tarbush seedlings appeared more susceptible to drought-caused mortality than seedlings in full sun. Survival rates of seedlings beneath the canopy of adults were significantly lower than those located outside the canopy (P<0.05 for all variables) :
|Survival rates (%) of tarbush seedlings under and outside of adult tarbush canopy cover from 60 to 300 days after the end of the rainy season (15 September) |
|Days||Under adult canopy||Outside adult canopy|
These data suggest that the probability of a tarbush seedling reaching the juvenile stage was very low under any conditions .
Tarbush grows taller on moist than dry soil [41,75,131]. In the Rio Grande Valley, tarbush occasionally occurred on sandy soil and infrequently on shallow soil underlain by caliche, but reached its best development as a community on soils that received some run-off water. The largest individuals were observed in or along washes, although average height of plants along washes did not differ significantly from that of upland plants . Because desert grasses and forbs generally depend on water from the same soil layers as tarbush, tarbush likely competes directly with these species for water. Thus, the ability of tarbush seedlings to rapidly develop root biomass was hypothesized to be critical for establishment . Roots of tarbush seedlings can grow >16 inches (41 cm) in <1 year (see Roots) .
Herbivory may be an important cause of tarbush mortality. In Durango, Mexico, browsing did not cause seedling mortality, but many dead juvenile tarbush plants were observed with all of their branches browsed, most likely by jackrabbits . On the piedmont slopes of the Doña Ana Mountains, jackrabbit herbivory reduced the size and vigor of tarbush plants, and 47% of browsed individuals died .
Vegetative regeneration: As of this writing (2010), information regarding tarbush vegetative regeneration is largely anecdotal. Barrow  stated that tarbush "commonly" propagates asexually. On the plains below the Guadalupe Escarpment, prolonged freezing weather killed tarbush plants "to ground level" , indicating some sprouting may have occurred. Campbell's  observation that tarbush can survive wind action exposing its roots "because it spreads vegetatively by sprouts" suggested that tarbush may spread by sprouting from roots. He further stated that tarbush "spreads by vegetative means so that its advance...is very steady, once it becomes established" . However, Scifres  reported that tarbush sprout development was from stem sections, and that tarbush spreads primarily via seeds. Noting that tarbush is easily killed by herbicide, Tschirley  concluded that tarbush was a "weak sprouter". As of this writing, no herbicide study reported tarbush sprouting after herbicide treatment (e.g., [33,50,60,102,103,127,139]). In the San Simon Valley of southeastern Arizona, mammal (black-tailed jackrabbit, desert cottontail, and white-throated woodrat) browsing appeared to stimulate new growth on tarbush, with new stems growing below the browsed points . In contrast, on the piedmont slopes of the Doña Ana Mountains, New Mexico, tarbush plants that were moderately to heavily browsed by jackrabbits showed no evidence of new stem growth below browsed points, although the leaves on browsed stems were visibly larger than the leaves on unbrowsed plants . Other researchers reported that tarbush can replace its leaves after defoliation. Tarbush in western Texas and southeastern Arizona apparently compensated for insect-caused damage to leaves in early spring by producing new foliage by midsummer . After herbicide application in late winter, tarbush refoliated several times during the 1st posttreatment growing season on the western Edwards Plateau, Texas . In south-central New Mexico, after a dry winter and spring, tarbush plants produced small, scale-like leaves in May and early June. These plants shed the small leaves and produced a new set of larger leaves as moisture availability increased in summer .
Apparently, tarbush prefers full sun, fine to medium soil textures, soil pH from moderately alkaline to strongly alkaline, and shallow to moderate soil depths.
Topography: Tarbush-dominated communities commonly occur as bands on alluvial flats and plains below the slopes of hills and mesas, in patches on the edges of tobosa or burrograss swales, along drainages that dissect the plains, and on piedmonts and mesas where it often occurs within creosotebush habitat. Rarely, tarbush habitats occur on steep, rocky slopes in a transition zone between creosotebush communities and upland desert grasslands. Tarbush also occurs near terrace edges and erosional escarpments where shifting sands, often dominated by mesquite (Prosopis spp.), encroach upon tobosa and burrograss habitats [11,13,69,75,84,121,153].
Habitats dominated by tarbush typically occur on nearly level to gently sloping sites on all aspects. In the basin and range physiographic province in southeastern Arizona, tarbush occurred most frequently on flat (<10% slope) and dissected topography on alluvial landforms, but occurred on a range of slope angles averaging <5% to >45% and on all aspects .
Elevation: Across its distribution in the United States, tarbush occurs from 2,300 to 6,900 feet (700-2,100 m) [15,43,69,104,118,121]:
|Elevational ranges reported for tarbush across its geographic distribution in the United States|
|Cochise County||3,500-5,000 feet (1,100-1,500 m) |
|southeastern Arizona||4,300-5,400 feet (1,300-1,650 m) |
|southeastern Arizona||primarily from 3,800-5,000 feet (1,200-1,500 m) |
|New Mexico||throughout||3,500-6,500 feet (1,100-2,000 m) |
|throughout||4,600-6,900 feet (1,400-2,100 m) |
|Texas||Trans-Pecos||2,300-6,500 feet (700-2,000 m) |
|Del Norte Mountains||4,500-4,700 feet (1,370-1,430 m) |
Soils: Tarbush dominates soils that are shallow to moderately deep, fine-textured silt or clay loams, often calcareous, and sometimes with impermeable or semi-permeable caliche or argillic horizons . Variation in parent materials and exclusion of tarbush by creosotebush in the most xeric, shallow soils may in part determine tarbush's distribution and abundance .
Texture: Tarbush grows in soils with a wide range of textures . Most soils supporting tarbush are moderately fine-textured to moderately coarse-textured . Tarbush often dominates "heavy" silt or clay soils with some gravel near the surface (e.g., [1,9,13,28,32,49,67,108,111,155]). Tarbush also grows on sands and sandy loams [6,11,16,67]. In the San Simon Valley, tarbush dominated a site with deep, well-drained, gravelly sandy loam soils . Tarbush occurred occasionally on mesquite sand dunes in southeastern New Mexico . A creosotebush-tarbush community occurred on sandy or gravelly soil overlying a bed of Tornilla Clay in the Tornilla Clay beds area of western Texas .
Depth: Soils supporting tarbush are shallow to moderately deep, although tarbush seems to prefer moderately deep soils [11,19,121]. Tarbush grows intermixed with creosotebush, but tarbush dominates on soils that are deeper than those in areas where creosotebush dominates [19,55]. In the San Simon Valley, where the soil was shallow (9 inches (24 cm) deep) over a dense, continuous caliche layer, creosotebush dominated the shrub cover (84%) and tarbush occurred with 5% cover. In areas where the soil was deeper (24 inches (60 cm) deep), finer textured, and had less carbonate and a discontinuous caliche layer, tarbush dominated the shrub cover (44% cover) and creosotebush was sparse (<1%) . In Cochise County, Arizona, a soft, unconsolidated caliche layer was considered typical of tarbush communities .
pH and parent materials: Tarbush occurs on mildly to strongly alkaline soils (range: 7.7-8.7) [9,28,67,108,130,132]. On a south-central New Mexican bajada, the creosotebush-tarbush association occurred on soils with a pH of 7.7 . In Brewster County, Texas, the creosotebush-tarbush association occurred on soils with a pH ranging from 8.1 to 8.6 and the tobosa-tarbush association occurred on soils with a pH of 8.7 . Tarbush communities occurred on soils with pH of 8.4 at the Jornada Experimental Range . In Cochise County, Arizona, average soil pH was 8.5 in tarbush communities .
Tarbush occurs in soils derived from many parent materials. Tarbush most often occurs in limestone or calcareous soils [11,19,43,69,104]. Limestone is the predominant parent material in the Chihuahuan Desert, although gypsum and igneous rocks are parent materials in some areas [84,86,132]. Tarbush may occur on soil derived from igneous rocks but is absent or rare on gypsic soils [11,157]. O'Laughlin  concluded that gypsiferous soils were the only soils from which tarbush has been found to be consistently absent. Unusually, Reid and others  reported scattered tarbush on gypsiferous soil in the gyp dropseed alliance in New Mexico. Tarbush frequently occurs on alluvial soils. In the Del Norte Mountains, Texas, tarbush was most common on deep, fine alluvial soils . In southeastern Arizona, tarbush occurred most frequently on alluvium parent materials (73% of plots) . Calculations by Chew and Chew  using the data of Gardner (1959 cited in ) gave the following creosotebush:tarbush cover ratios in soils of different parent materials: 1.4 on alluvium, 1.2 on limestone conglomerate, 0.9 on limestone, and 0.2 on shale. Tarbush was sparse on transported andesite (Gardner 1959 cited in ).
Moisture: Tarbush prefers relatively moist sites that receive some run-off water. Bajadas, or piedmont plains, are the weakly sloping plains that connect the mountains and hills with bottomland playas (ephemeral lakes), arroyos, and floodplains. Bajadas receive some water by sheet flow and also lose some water by run-off . Tarbush often occurs on bajadas and in and on the edge of adjacent bottomlands [100,136]. Tarbush appears to avoid poorly drained areas such as playas and excessively drained areas such as high-elevation mountain slopes, preferring the moderately well-drained bajadas . Tarbush often occurs within and adjacent to tobosa and burrograss grasslands [10,13,28,43]. These grasslands are often called "tobosa swales" or "burrograss swales" because they occur in depressions where surface run-off accumulates and stands for several days . On the Jornada Plain, sites with abundant run-off water from high-elevation areas in the Jornada Plain typically supported abundant stands of tobosa with lesser amounts of tarbush, but sites that were occasionally flooded by run-off water were dominated by tarbush . In Cochise County, Arizona, tarbush individuals were more abundant and visibly more vigorous in that portion of the tarbush community nearest the ecotone with tobosa, where soil moisture availability appeared to be more favorable . In New Mexico, tarbush occasionally occurred on the edges of dried playa beds as long as the soil was not sandy, with burrograss extending toward the center of the bed. Tarbush did not establish in the center of the playas, apparently because it cannot tolerate standing water  and/or possibly high salt concentrations  that sometimes occur in playas. Tarbush also frequently occurred along arroyo margins in southern New Mexico [26,73,111]. In south-central and southwestern New Mexico, tarbush occurred in clay soils on barren or sparsely vegetated flats and bottomlands where moisture was often abundant due to run-off water from surrounding areas; in these areas, soil erosion was often "severe" and deep gullies were common . Tarbush occurred in washes in Brewster County, Texas  and the Rio Grande Valley . Herbel  described tarbush as a meshophyte and creosotebush as a xerophyte in the creosotebush-tarbush association. In contrast, Gehlbach  described tarbush as one of the most xerophytic dominant plants of the Guadalupe Escarpment of New Mexico and Texas.
Differences in soil moisture preference may in part explain tarbush and creosotebush distribution, with creosotebush tending to dominate the most xeric sites and tarbush tending to dominate more mesic sites . In San Luis Potosi, Mexico, creosotebush occurred in nearly pure stands except in places with high soil moisture, where tarbush occurred with creosotebush . At the Jornada Experimental Range, tarbush dominated sites primarily on clay loam soils with some gravel near the surface on sites that received some flood water. In contrast, tarbush occurred within creosotebush-dominated habitat on a variety of soils including low rolling ridges of the foothills and alluvial fans; well-drained areas of deep sand; deep, "heavy" soil; shallow, stony soils underlain by caliche; and arroyo beds .
Climate: Tarbush primarily occurs in the Chihuahuan Desert. Average annual precipitation in the Chihuahuan Desert ranges from 5.9 to 15.7 inches (150-400 mm) . Most (>50%) precipitation in the Chihuahuan Desert occurs during convective thunderstorms during July to September, when evapotranspiration rates are high [10,19,65,111]. Evaporation rates during summer may be up to 10 times the precipitation [42,111]. Thunderstorms are frequently of high intensity, so much of the rainfall becomes surface run-off and thus is unavailable to plants . Flash flooding and water erosion often occur in summer . Most winter precipitation occurs as low-intensity rainfall and occasionally as snow in winter and early spring . Late spring [19,111] and late fall  are commonly dry.
Interannual variability in precipitation is high, and drought is common in the Chihuahuan Desert [10,31,111,121]. Temperatures are often extreme and vary from -9 to 108 °F (-23 to 42 °C) . Mean maximum monthly temperature (97 °F (36 °C)) occurs in June. Temperatures are ameliorated in July by the beginning of summer rains. Mean minimum monthly temperature (56 °F (13 °C)) occurs in January [19,31,111]. The frost-free season averages 200 days/year, but the effective growing season (the duration of favorable soil moisture and temperatures) is typically <90 days and occurs from July to September [31,111].
Weather extremes may kill tarbush. In the San Simon Valley, an unusually long period of freezing weather (4 days) killed tarbush stems . On the plains below the Guadalupe Escarpment, prolonged freezing weather killed tarbush plants "to ground level" . At the Jornada Experimental Range, some tarbush plants died after successive years of drought, which set back tarbush encroachment into tobosa and other swale habitats . In Durango, Mexico, water-stressed tarbush seedlings had no leaves in May, whereas unstressed tarbush seedlings retained their leaves .
Primary disturbances in communities with tarbush are grazing, fire, drought, and flooding [72,123,141]. Tarbush has increased in density and distribution due to overgrazing by livestock, reduced fire frequency and severity, and climate change since the late 1800s [11,27,29,121]. Thus, tarbush is often considered "invasive" in desert grasslands [11,28,49,56,111], and desert grasslands that have become dominated by shrubs are often referred to as "degraded" because they have increased soil erosion and reduced forage value for livestock and wildlife [14,18,27,104,162]. Tarbush may spread into black grama grasslands  but primarily spreads into communities on clay soils dominated by tobosa and burrograss [11,51,111]. While tarbush has spread into many grasslands, creosotebush has encroached into tarbush habitats in some areas since the late 1920s [11,48].
Tarbush primarily increases in desert grassland communities that have been "degraded" due to fire exclusion, overgrazing, or soil erosion. Herbel  noted that tarbush spread into sites dominated by black grama or tobosa, after which sites are deteriorated by soil erosion and the formation of drainages. He described the creosotebush-tarbush community as a "persistent subclimax" of the black grama-tobosa shrub steppe . In an early study at the Jornada Experimental Range, the tarbush-tobosa community was described as a "climax" plant community, and the tarbush/burrograss community was described as seral to this climax . Subsequent studies on the Jornada Experimental Range reported that tarbush quickly spread into areas where the conversion of desert scrub to desert grasslands was attempted by use of mechanical methods [111,141]. In a study of the Big Bend Region of Texas, Muller  concluded that the creosotebush-tarbush association is capable of forming a stable climax community. In Brewster County, Texas, the creosotebush-tarbush association was considered climax vegetation for the desert plains in the region . In a 1975 review, Tueller  concluded that in southern desert grasslands, a climax community dominated by grasses retrogressed after disturbance to a "disclimax" of short-lived perennial grasses, half-shrubs, cacti, and shrubs including tarbush, creosotebush, viscid acacia, and mesquite. Another study described desert scrub as part of the desert grassland disclimax in which shrubs become dominant in grassland communities following disturbance .
As tarbush cover increases, grass cover typically declines [11,41]. In a tobosa-tarbush association in Brewster County, Texas, tarbush and other shrubs were usually spaced 2 to 3 feet (0.6-0.9 m) apart, and bare ground was particularly abundant around tarbush plants . This suggests that habitats with greater tarbush dominance are likely to have increased bare ground and less grass cover. However, tarbush spread into desert grasslands appears to reduce grass cover less than mesquite or creosotebush spread [11,41]. In the Rio Grande Valley, grass cover in tarbush communities was usually greater than it was on sites dominated by creosotebush or other shrubs in habitats with similar shrub cover. Grass cover in tarbush communities (primarily burrograss and tobosa) ranged from 0.06% to 1.58%, and that on creosotebush communities (primarily fluff grass and burrograss) ranged from 0% to 0.77% . Shrub cover in mesquite communities was greater and grass cover less than on tarbush or creosotebush communities. The author noted, however, that as tarbush cover increased, grass cover declined. Tarbush's association with high grass cover was attributed to its preference for more favorable sites , such as those with deep and moist soils. At the Jornada Experimental Range, Buffington and Herbel  observed that "some areas invaded by tarbush still have a good understory of grass", but noted that livestock forage production was "negligible" in many creostebush-dominated areas. In the Rio Grande Valley, tarbush-dominated habitats always had some grass among the tarbush plants, and tarbush plants branched from ground level; whereas in creosotebush-dominated habitats with tarbush, grass cover was lower and tarbush plants appeared to have trunks because soil had eroded from their roots .
Creosotebush spread may reduce habitat quality for tarbush as well as for grasses. In creosotebush-tarbush communities in southeastern Arizona, a negative correlation between creosotebush density and tarbush density indicated that creosotebush excluded tarbush in the habitat (r= -0.43; P<0.01) . In the Rio Grande Valley, creosotebush populations were expanding and dominance was increasing in areas dominated by tarbush. Young creosotebush plants grew on the edge of tarbush communities, but no young tarbush plants grew in creosotebush communities. This suggested that creosotebush spread into tarbush communities was due to changes in the complex of soil factors affecting these species distributions, especially the loss of surface soil due to erosion. Mesquite did not appear to be encroaching into tarbush communities . In a study of vegetation changes from 1858 to 1963 in desert grasslands of the Jornada Plain in southeastern New Mexico, creosotebush spread and excluded tarbush in communities historically dominated by tarbush. Mesquite also spread into tarbush communities. Grass cover decreased with the spread of both tarbush and creosotebush, although "there has been a much greater reduction of grass cover on creosotebush and mesquite areas than on tarbush areas". Furthermore, where tarbush spread into grasslands, loss of grass cover was slow, in contrast to the rapid replacement of grasses by mesquite . In a subsequent study of vegetation changes in the Jornada Basin to 1998, Gibbens and others  agreed that much of the increase in creosotebush over the 150-year study "occurred at the expense of tarbush", particularly on bajada slopes. Overall, tarbush declined in areas where it was once dominant and spread in areas formerly dominated by burrograss and tobosa . Due to its tendency to be replaced by creosotebush in some disturbed habitats over the past 100 to 120 years, Dick-Peddie  proposed that the absence of tarbush in desert scrub may indicate succession from desert grassland to desert scrub.
Tarbush cover is often greater on undisturbed sites than on severely disturbed sites. In southeastern Arizona, where tarbush was removed from a site in San Simon Valley, tarbush density was higher on ungrazed sites (6.3 plants/60 m²) and grazed sites (7.9 plants/60 m²) than on root-plowed sites (0.4 plants/60 m²) 16 years after disturbance . Another study in the San Simon Valley reported higher tarbush cover on undisturbed sites (6.0 plants/500 plots) than disturbed sites (grazed, burned, and burned and grazed sites; 0-2.2 plants/500 plots) 2 years after disturbance . See Plant response to fire for more information on this study.Establishment of tarbush after disturbance is apparently slow, but tarbush can dominate a site within 60 years after disturbance. Rango and others  examined tarbush habitat in the Jornada Basin where all shrubs were removed by grubbing in 1937 and 1939 and noted that 63 years after the 2nd grubbing, cover of tarbush, Berlandier's wolfberry, and bush muhly (Muhlenbergia porteri) increased to approximately the same as that on control plots the year of the treatment. Control sites had many small shrubs, whereas treated sites had few but large shrubs . In another study in the Jornada Basin at the Jornada Experimental Range, a desert grassland site likely historically dominated by black grama, bush muhly, and spike dropseed (Sporobolus contractus) became dominated by tarbush within 57 years of increased cattle grazing and periods of extended severe droughts. Within 140 years, the site was dominated by creosotebush with honey mesquite and tarbush as subdominants .
Immediate fire effect on plant: As of this writing (2010), no direct observations of immediate fire effects on tarbush were recorded in available literature. However, fire likely kills tarbush
Postfire regeneration strategy :
Fire adaptations and plant response to fire: Fire adaptations: Due to its high resin content (see Botanical description) and "weak" sprouting ability (see Vegetative regeneration) fire likely kills tarbush plants. Tarbush likely establishes from seed after fire. It is unclear as of this writing (2010) whether tarbush seeds are killed by fire. Information on seed sources (on- or off-site) was limited. Some evidence suggests that tarbush lacks a persistent (>2 years) seed bank. This, coupled with short dispersal distances of seeds, suggests that establishment of tarbush by seed after extensive, stand-replacing fire is likely very slow. Anecdotal evidence that tarbush may spread by sprouting from roots  suggests that it could reproduce vegetatively after fire as long as the roots are not damaged; however, no studies as of this writing (2010) reported tarbush sprouting after fire. Due to limited studies, it is uncertain how quickly tarbush establishes after fire. Studies are needed on tarbush fire ecology.
Plant response to fire: Because tarbush increases slowly after disturbances that remove shrubs and may not regain dominance for up to 60 years (see Successional Status), tarbush likely decreases after fire and then increases slowly over time. Droughts likely slow the rate of tarbush recovery following fire, but as of this writing (2010), no information is available. At the McGregor Missile Range, Fort Bliss, Texas, prescribed fire was applied in June in a creosotebush-tarbush community. Immediately after the prescribed fire, grass and shrub cover were reduced and bare ground increased. Tarbush mortality averaged 29.1%. No information was provided on prefire cover or the fire's severity or patchiness . A late May prescribed fire in a desert grassland with low tarbush cover (<1%) reduced shrub cover to zero, reduced grass cover from 46% to 2%, and increased bare ground cover from 14% to 51% during the 1st postfire year . In the San Simon Valley, prescribed burning was applied in June to a grazed and an ungrazed desert scrub community on a site historically dominated by desert grassland. Because there were insufficient fuels to carry a fire, all individual shrubs, grasses, and standing dead annuals were burned individually with a propane torch, resulting in 100% open ground and all plants at least top-killed. On ungrazed sites, tarbush cover was 0% immediately after burning; 2.2% 3 months after burning; and 0.8% 2 years after burning. This indicated substantial tarbush mortality after initial postfire establishment. It was unclear whether postfire establishment was by sprouts or seedlings. Grazed sites (both burned and unburned) had no tarbush and untreated sites had the highest tarbush cover throughout the study :
|Mean tarbush cover across 4 treatments 3 and 24 months after prescribed burning and livestock grazing |
|Time since treatment||
Number of tarbush plants/500 plots
|Burned||Grazed||Burned and grazed||Untreated|
FUELS AND FIRE REGIMES:
Fuels: Stand structure in plant communities where tarbush occurs is typically open with scattered shrubs, grasses, and forbs, and extensive rock and bare ground. Vegetation may vary from very open to moderately dense (e.g., [10,14,55,65,121]). Potential fire spread depends greatly on stand structure, which is influenced by site conditions. The frequency and severity of fires in desert ecosystems are highly contingent on the degree and rate of grass growth to serve as fuels, which may be determined by the timing and amount of precipitation prior to and following fires, plant physiology, soil characteristics, and the degree of livestock grazing [31,64,91]. In general, productivity—and consequently fuel load—is low in Chihuahuan Desert communities except when there is a year of exceptional winter rains resulting in a heavy stand of annuals to serve as fuels .
Total plant cover in communities where tarbush occurs is typically sparse (<40%). Rock and/or bare ground cover commonly exceeds 60%, and litter cover is often <10% (e.g., [4,41,51,67,92,129]). At the Jornada Experimental Range, tarbush-dominated communities had 17% total shrubs, 21% herbs, 57% bare ground, and 5% litter . In Hidalgo County, New Mexico, tarbush occurred in creosotebush-broom snakeweed habitat with approximately 20% total shrubs, 70% rocks and bare ground, and 10% litter . On the Stockton Plateau in western Texas, in tarbush-burrograss communities, cover ranged from 13% to 21% plants, 69% to 82% mineral soil and rock, and 2% to 4% litter. In tarbush-purple threeawn communities, cover ranged from 32% to 43% plants, 27% to 34% rock and mineral soil, and 32% to 40% litter . In Cochise County, Arizona, tarbush-dominated communities had a mean cover of 32% perennials, 10% annuals, 61% bare soil, 20% rock, and 7% litter . Grass cover typically decreases as tarbush cover increases, suggesting that tarbush-dominated habitats are likely to have sparse, widely spaced fine fuels, and fire is unlikely to carry well. However, tarbush-dominated habitats may be more likely to carry fire than creosotebush-dominated habitats because of relatively greater fine fuel loads in tarbush-dominated habitats . See Successional Status for more information on this topic.
The amount of resin a plant contains affects how readily and intensively it burns. Although not reported as of this writing (2010), the "extremely" resinous foliage and stems of tarbush  may make it highly flammable.
Tarbush growth habit.
Photo courtesy of Russ Kleinman and Deming Gustafson, Burro Mountains, Hoodoo Canyon, Gila National Forest
Fire regimes: Historically, fire was a natural event in Chihuahuan Desert ecosystems, although some parts of the Chihuahuan Desert may have never experienced fire historically [12,29,64,95]. Lightning-caused fires occurred just prior to and throughout the growing season, particularly during June when dry conditions persist and high winds are common .
Tarbush occurs as scattered individuals in Chihuahuan Desert grasslands where fire was historically frequent (<10-year intervals) [31,163]. Fire-return intervals coincided with the time required for herbaceous fuels to accumulate to the point where they could carry fire (Cable 1967 cited in ). Historically, frequent fires interacted with other factors including topography, soil, herbivory, and herbaceous plants to restrict woody plant establishment in grasslands [29,63,64,65,95]. Even occasional fires in desert grasslands may have prevented establishment of woody species, thus maintaining grasslands [65,112,144]. Tarbush occurs most frequently in desert scrub communities. Historically, Chihuahuan Desert scrub was restricted to ravines, knolls, and sites where conditions were unfavorable for grasses, and consequently where fuels were sparse and would not carry fire over large areas [19,44,86]. Fire-return intervals in desert scrub were greater than in desert grasslands on average . When fires occurred they were typically stand replacing. Desert scrub was most likely to burn in the ecotone where it bordered desert grassland .
Burgess  commented that "it would be wrong...to assume that fire is a universal feature of desert grasslands". Some parts of the Chihuahuan Desert may have never experienced fire historically due to a combination of patchy vegetation and low fuel loads [12,29,64]. On the Jornada Plain, no extensive fires were reported historically, and fire was not considered a factor in the maintenance of these grasslands . No fires were reported historically at the Mapimi Biosphere Reserve, Durango, Mexico . Grassland fires leave behind little to no direct evidence of fires so estimates of historic fire frequency and extent are based on historical accounts of early settlers and indirect evidence [64,95]. Nonetheless, most researchers agree that fire has historically been common in most desert grasslands . For reviews of fire history in North American desert ecosystems in general and Chihuahuan Desert ecosystems in particular, see these sources: [7,31,95]. See the Fire Regime Table for further information on fire regimes in vegetation communities in which tarbush may occur. Find further fire regime information for the plant communities in which this species may occur by entering the species name in the FEIS home page under "Find Fire Regimes".
FIRE MANAGEMENT CONSIDERATIONS:
Since the late 1800s, frequency and severity of fires in Chihuahuan Desert ecosystems was lessened directly by fire exclusion and indirectly by livestock grazing. Overgrazing by livestock decreased cover and biomass of herbaceous species necessary to carry fire. Grasses stabilize desert soils, and reduction of grasses by overgrazing led to soil erosion and reduced likelihood that grasses would return to dominance. Drought periods and possibly gradual warming of the climate of the Southwest enabled trees, shrubs, and cacti to spread into desert grasslands (e.g., [7,19,29,31,31,64,65,70,87,118]). Tarbush spread into desert grasslands of the Jornada Plain from 1858 to 1963 may have been due, in part, to reduced fire frequency resulting from overgrazing and a reduction of fine fuels .
Prescribed fire is often recommended for preventing the encroachment of shrubs such as tarbush into desert grasslands [7,64]. Because tarbush may not reproduce until it is >10 years old (see Seedling establishment and plant growth), prescribed fires occurring at <10-year intervals are likely to eliminate tarbush. Humphrey  surmised that prescribed burning in desert grasslands at 5- to 10-year intervals would reduce abundance of shrubs such as tarbush and maintain desert grasslands. He cautioned, however, that heavily grazed desert grasslands typically do not have enough fuel to effectively carry a prescribed fire that would be "hot" enough to kill large shrubs . In a 1993 review of fire effects on mixed desert grass-scrub communities, prescribed fire was not recommended for desert habitats with moderate to high shrub cover because there is typically not enough fine fuel to carry a fire. The authors suggest a minimum fine fuel load of 600 lb/acre (674 kg/ha) to support prescribed fire for controlling shrubs. Burroweed, broom snakeweed, creosotebush, young mesquite, and cactus are mentioned. The researchers recommended applying prescribed fire during dry seasons that follow 1 to 2 years of above-average summer precipitation, when enough fuel has accumulated and grasses are most likely to increase after fire . Summer prescribed fires were generally considered more likely to damage shrubs than winter fires . A 1975 review recommends against prescribed fire in several areas in the Chihuahuan Desert because fires that kill shrubs such as tarbush usually kill grasses too, and fires that spare grasses may not kill shrubs . Although their study site did not include tarbush, Rogers and Steele  recommended a conservative view toward use of fire in deserts because of slow recovery rates.Presence of nonnative invasive species such as lovegrass (Eragrostis spp.) may alter fire regimes in desert grasslands and limit the effectiveness of prescribed fire for restoring native grasses . Lehmann lovegrass (E. lehmanniana), common in parts of the Chihuahuan Desert including the Jornada Experimental Range , increases after fire, produces more fine fuel than native grass species, and probably contributes to increased fire spread . In a review, McPherson  suggested that a positive feedback pattern may develop between lovegrass and fire, resulting in further reduced forage in desert ecosystems for livestock and wildlife. Such as feedback loop could cause fires to occur more frequently than in the 1900s; however, fires would likely still be less frequent than occurred historically. For more information on the interactions of fire and nonnative invasive species, see the FEIS review for Lehmann lovegrass and other species of interest.
FEDERAL LEGAL STATUS:
Information on state- and province-level protection status of plants in the United States and Canada is available at NatureServe.
IMPORTANCE TO WILDLIFE AND LIVESTOCK:
Tarbush is unpalatable and not generally used by wildlife or livestock, unless little else is available [75,131].
Palatability and nutritional value: Tarbush leaves have high concentrations of plant secondary compounds . The peppery, bitter quality of tarbush herbage makes it unpalatable to wildlife and livestock [25,69,75].
Wildlife: Tarbush is browsed by black-tailed jackrabbits [20,89,125,135], desert cottontail, and white-throated woodrats . Heavy jackrabbit browsing may decrease tarbush abundance. At the Jornada Experimental Range, tarbush cover decreased in lagomorph-grazed areas compared to exclosures, probably due to browsing of the tarbush canopy and seedlings . On the piedmont slopes of the Dona Ana Mountains, New Mexico, jackrabbits preferentially browsed tarbush in creosotebush-tarbush communities . Chew and Chew  reported that in addition to eating tarbush, black-tailed jackrabbits, desert cottontail, and white-throated woodrats in the San Simon Valley "pruned" tarbush, removing an average of 46% to 48% of the volume of individual tarbush plants along transects. Some tarbush plants were browsed close to the ground. However, much of the tarbush browse was uneaten and found lying on the ground next to the plants .
Tarbush fruit and browse may be toxic to some wildlife species, particularly if they feed on it exclusively. Pronghorn antelope in the Trans-Pecos region of Texas reportedly died from tarbush consumption because of a lack of other available forage . As of this writing (2010), it is unclear whether small mammals and other granivores eat tarbush seeds. Captive Merriam's kangaroo rats obtained from the San Simon Valley ate tarbush seeds when presented with pure diets of the seeds. However, they lost weight rapidly . Tarbush seed predators include fly (Euarestoides acutangulus) and beetle (Smicronyx spretus and S. profusus) larvae (, Mauchamp 1992 cited in ) and possibly ants (order Hymenoptera) .
Tarbush is host or alternate host to >90 species of insects, spiders, and arthropods throughout its distribution in the United States and northern Mexico [17,35,122]. Many of these feed on tarbush and some, such as the leaf beetle Zygogramma tortuosa, may cause defoliation leading to reduced seed production in tarbush . For more information on this study, see Seed production. Two invertebrates, a grasshooper (Ligurotettix planum) and a moth (Bucculatrix flourensiae), apparently feed exclusively on tarbush, although they do not seem to affect tarbush growth, seed production, or mortality .
Livestock: Tarbush is unpalatable and not generally used by livestock, unless little else is available [75,131]. The buds, flowers, fruit (immature or ripe), and possibly seeds are toxic to domestic sheep, domestic goats, and cattle [30,75,131,135]. Tarbush herbage appears less toxic to livestock than other parts of the plant. Cattle, domestic sheep, and domestic goats can apparently consume modest quantities (≤30%) of tarbush forage in mixed diets without ill effects [2,61,74,83]. However, a diet exclusively of tarbush leaves may lead to malnutrition, weight loss, and possibly death . Some researchers reported high nutritive value of tarbush leaves that met the requirements of livestock but also high values of "anti-nutritional factors" such as phenolics [30,35].
Cover value: Tarbush provides shade for animals in summer . It is used as escape cover and foraging sites for lizards, such as the western whiptail and side-blotched lizard [4,115], small mammals, such as the white-throated woodrat, cactus mouse, western harvest mouse, and Marriam's kangaroo rat [4,8], and birds such as sparrows and northern mockingbird . In Fort Bliss, Texas, 5 species of birds nested in tarbush, and tarbush was the 4th most frequently used nest plant species in both arroyos and upland habitats . Despite the fact that tarbush provides "few hiding places" , the Pecos clicker grasshopper (Ligurotettix planum) lives and feeds almost exclusively on tarbush [109,122,129].VALUE FOR REHABILITATION OF DISTURBED SITES:
OTHER MANAGEMENT CONSIDERATIONS:
Tarbush is unpalatable to livestock, and it increases as overgrazing reduces palatable forage plants, often becoming dominant on overgrazed sites [18,29,43,121]. Overgrazing reduces grass cover in desert grasslands below the levels where they can carry fire, thus reducing fire frequency and severity [64,163]. Mechanical controls (e.g., hand grubbing, bulldozing, and root plowing) and subsequent seeding [59,96,126], herbicide application (e.g., [33,50,60,102,103,127,139,145,154]), and prescribed fire [38,98,149] have been used in tarbush-dominated areas to reduce or eliminate tarbush and other shrubs and increase grasses (reviews by [56,57,148]). Biological control methods have been considered for tarbush [27,122], but as of this writing (2010) no such methods have been implemented either in the United States or Mexico. Results of studies attempting desert grassland restoration in habitats with tarbush were varied. Treatments were generally successful at reducing or removing tarbush in the short term, but in some cases desirable native grasses (e.g., black grama) did not increase, unpalatable native (e.g., fluff grass and broom snakeweed) or nonnative (e.g., lovegrass) grasses increased or remained the same, and tarbush and other shrubs returned [13,27,96,126,148,150]. The rate, direction, and amount of vegetation change observed after removal of either grazing or shrubs varies depending on many complex and interrelated factors, including weather, initial and posttreatment species composition and abundance, and nearby seed sources [6,149].
Some researchers reported reduced tarbush and other shrub cover and increased perennial grass cover in habitats where grazing was excluded. Near the Black Mountains in Catron County, New Mexico, 25 years of grazing exclusion in honey mesquite-tarbush habitat eliminated tarbush, reduced honey mesquite, decreased fluff grass, and increased black grama . In the San Simon Valley, tarbush-dominated areas protected from livestock grazing for 18 to 19 years had increased abundance of palatable perennial grasses, particularly black grama, compared to grazed sites (P<0.02) .
In contrast, others researchers reported little or very slow change in cover of shrubs and grasses with protection from grazing for up to 20 years in habitats with tarbush (e.g., [6,18,59,149]). In southeastern Arizona, tarbush and unpalatable fluff grass were more abundant on sites grazed by cattle during and prior to the study than on sites ungrazed for 16 years (P<0.05 for both variables). Palatable native perennial grasses such as bush muhly and Arizona cottontop (Digitaria californica) were similar between grazed and ungrazed sites; thus grazing exclusion did not improve cattle forage. In broom snakeweed-tarbush-burroweed (Isocoma tenuisecta) communities in the San Simon Valley, there was little difference between a site ungrazed for 20 years and a nearby grazed site. However, a site ungrazed for 39 years had significantly higher native perennial grass cover (e.g., black grama, tobosa, cane bluestem (Andropogon barbinodis)) and significantly lower shrub cover than a nearby grazed site, and nearly all the increase in native perennial grass cover occurred during the latter 20 years (P<0.03 for all variables). Tarbush cover was similar on grazed (4.8%) and ungrazed (4.4%) sites after 39 years of grazing exclusion .
Precipitation patterns influence plant growth and persistence in desert ecosystems , and weather likely plays a substantial role in the effects of disturbance on tarbush populations. In Big Bend National Park, historic records over a 26-year period after removal of livestock from desert grassland communities indicated that during the first 5 years of livestock exclusion, a period of drought, little change in cover was observed. Tarbush and creosotebush cover increased from 5 to 12 years after livestock exclusion, a period of summer drought and frequent wet winters. From 12 to 26 years after livestock exclusion, cover and density of forbs, perennial grasses, and most shrubs except creosotebush increased when summers were wetter than average. No control plot was available for comparison, so the authors could not isolate the effects of livestock grazing exclusion from the effects of weather .
Extended dry periods strongly influence dominance in desert plant communities. Buffington and Herbel  speculated that periodic drought most likely contributed to tarbush spread into burrograss and tobosa grasslands . Typically, the lower, most poorly drained parts of basins are dominated by tobosa. On bajadas, the slightly better drained areas fringing these flats, tarbush often dominates, replacing tobosa. Thus during periods of sustained drought, as basins become drier, tarbush is able to spread into tobosa swales. Further up slope, on excessively drained sites, creosotebush replaces tarbush. As bajadas become progressively drier due to sustained drought, creosotebush spreads into tarbush-dominated sites .Long-term climate changes are likely to cause vegetation changes in desert ecosystems. Rising carbon dioxide levels predicted with global climate change are predicted to favor C3 woody plants such as tarbush more than herbaceous plants, particularly C4 grasses [27,91]. This relationship may partially account for the increase in shrubs such as tarbush in desert grasslands in the early 1900s . However, it was difficult to determine whether vegetational changes were due to carbon dioxide, climate, or other causes such as overgrazing . Increasing greenhouse gas concentrations in the atmosphere and increasing temperatures may result in either increased fire frequency in desert ecosystems due to hotter, drier weather, or to decreased fire frequency due to decreased fine fuel production. Climate may not only become drier but also more variable as a result of increasing greenhouse gases. The impacts of this change are likely to be complex and difficult to predict .
|Fire regime information on vegetation communities in which tarbush may occur. This information is taken from the LANDFIRE Rapid Assessment Vegetation Models , which were developed by local experts using available literature, local data, and/or expert opinion. This table summarizes fire regime characteristics for each plant community listed. The PDF file linked from each plant community name describes the model and synthesizes the knowledge available on vegetation composition, structure, and dynamics in that community. Cells are blank where information is not available in the Rapid Assessment Vegetation Model.|
|Vegetation Community (Potential Natural Vegetation Group)||Fire severity*||Fire regime characteristics|
|Percent of fires||Mean interval
|Surface or low||15%||67|
|Desert grassland with shrubs and trees||Replacement||85%||12|
|Plains mesa grassland||Replacement||81%||20||3||30|
|Plains mesa grassland with shrubs or trees||Replacement||76%||20|
|Desert shrubland without grass||Replacement||52%||150|
|Southwestern shrub steppe||Replacement||72%||14||8||15|
|Surface or low||15%||69||60||100|
|Southwestern shrub steppe with trees||Replacement||52%||17||10||25|
|Surface or low||25%||35||25||100|
|Vegetation Community (Potential Natural Vegetation Group)||Fire severity*||Fire regime characteristics|
|Percent of fires||Mean interval
|South-central US Grassland|
|South-central US Shrubland|
|Southwestern shrub steppe||Replacement||76%||12|
Replacement: Any fire that causes greater than 75% top removal of a vegetation-fuel type, resulting in general replacement of existing vegetation; may or may not cause a lethal effect on the plants.
Mixed: Any fire burning more than 5% of an area that does not qualify as a replacement, surface, or low-severity fire; includes mosaic and other fires that are intermediate in effects.
Surface or low: Any fire that causes less than 25% upper layer replacement and/or removal in a vegetation-fuel class but burns 5% or more of the area [54,80].
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