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|Eastwood's manzanita over Hot Springs Canyon in the Santa Ana Mountains of southern California. Creative Commons image by Laura Camp.|
This review summarizes information on fire effects and related ecology of Eastwood's manzanita that was available in the scientific literature as of 2020.
Eastwood's manzanita is native to Oregon, California, and southern Mexico. It grows in nutrient-poor soils at a wide range of elevations. It grows primarily in chaparral but also in annual grasslands, oak scrub, oak and pine woodlands, and coniferous forests.
Eastwood manzanita is morphologically highly variable and has many accepted infrataxa. Some of these have protection status. Eastwood's manzanita regenerates by sprouting from the basal burl and from seed; sprouting is more common. Its seeds are dormant in the soil-stored seed bank; they require intense heat shock or chemicals leached from charred wood to germinate. Eastwood's manzanita occurs in all stages of chaparral succession.
Fire top-kills Eastwood's manzanita. It recovers from fire by sprouting and by establishing from seed. Fire can break dormancy of Eastwood's manzanita seeds. Eastwood's manzanita foliage and branches are highly flammable. Chaparral fires are stand-replacing, in part, due to the high flammability of Eastwood's manzanita and other chaparral species and the horizontal and vertical continuity of fuels.
Although Eastwood's manzanita foliage is unpalatable, its fruits provide food for many wildlife species. Its dense stands provide cover for small birds and mammals. Eastwood's manzanita provides watershed protection, particularly after fire, when it is among the first species to sprout.
Fryer, Janet L. 2020. Arctostaphylos glandulosa, Eastwood's manzanita. In: Fire Effects Information System, [Online]. U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station, Missoula Fire Sciences Laboratory (Producer). Available: http://www.fs.fed.us/database/feis/plants/shrub/arcgla/all.html .
Most research on the fire and general ecology of Eastwood's manzanita has been conducted in southern California, and virtually none in Oregon. In this Species Review, "historical" refers to the time before Spanish settlement (prior to 1770). This Species Review cites several reviews: [11,25,54,72,77,93,110].
Common names are used throughout this Species Review. See table A1 for a complete list of plant species mentioned in this review.FEIS abbreviation:
San Gabriel manzanita is recognized as a distinct species [138,142], although some authorities recognize it as subspecies of Eastwood's manzanita (Arctostaphylos glandulosa subsp. gabrielensis J.T. Keeley, M.C. Vasey & V.T. Parker) [3,16,27,60,78].
Hybrids: Campbell's manzanita is a hybrid of Eastwood's manzanita and woolyleaf manzanita . Putative hybrids of Eastwood's manzanita are reported from Mendocino County. These hybrids are apparently various combinations of the typical subspecies (Arctostaphylos glandulosa subsp. glandulosa), common manzanita, hoary manzanita, Roof's manzanita, and Stanford's manzanita .SYNONYMS
|For Arctostaphylos glandulosa subsp. adamsii:|
|For Arctostaphylos glandulosa subsp. crassifolia:|
|For Arctostaphylos glandulosa subsp. glandulosa:|
|For Arctostaphylos glandulosa subsp. mollis:|
|For Arctostaphylos glandulosa subsp. zacaensis:|
|Figure 1—Distribution of Eastwood's manzanita in the United States. Map courtesy of the U.S. Department of Agriculture, Natural Resources Conservation Service. [2020, June 11] . See Plants Database for distributions of infrataxa.|
United States: CA, OR  (fig. 1)
Mexico: BCN 
The climate within the distribution of Eastwood's manzanita is mediterranean, with mild winters and summer drought. Over 60% of California chaparral is in areas receiving between 10 to 30 inches (250-750 mm) of annual precipitation and where mean January daily temperature falls between 32 °F and 59 °F (0°C and 15 °C) .
Topography: Eastwood's manzanita has a wide elevational range . It occurs from 160 to 7,200 feet (50-2,200 m) [3,20], depending on location and infrataxon (see Baldwin et al. (2012)  for elevational ranges of infrataxa). It grows on slopes that range from flat to extremely steep and rugged , on all exposures. In the North Coast Ranges, it is most common on north-facing slopes . In southern California, it is most common on south- and west-facing slopes, above 3,200 feet (975 m) . However, in mixed chaparral on the Cleveland National Forest, Eastwood's manzanita is dominant on north-, west- and south-facing slopes. Its occurrence is positively associated with increasing elevation (P < 0.1) but not with aspect . It also grows on ridgetops and crests. Pure stands occur mostly on gentle slopes and flats . In the Santa Monica Mountains, Eastwood's manzanita grows in sandstone-derived soils on north-facing slopes, while birchleaf mountain-mahogany grows in andesite-derived soils on south-facing slopes .
Soils: Chaparral soils are generally shallow, rocky, and nutrient poor [11,72,141]. Eastwood's manzanita tolerates dry soils and drought [44,50,52,53,117]. Parent materials of soils supporting Eastwood's manzanita include sandstone, shale, granite, and volcanics [11,72]. Eastwood's manzanita also occurs on serpentine [17,60] and other ultramafic soils [2,17,72]. In the Pine Hills Ecological Preserve in El Dorado County, California, it grows in gabbro soils that are extremely acidic to very strongly acidic (pH 4-5) . Soil textures in which Eastwood's manzanita grows include clay and sand [46,158]. In maritime chaparral, Eastwood's manzanita grows in weathered sands in the fog belt .
Del Mar manzanita grows on sandstone-derived terraces near the sea .
Plant Communities: Eastwood's manzanita grows primarily in chaparral but also in annual grasslands , oak scrub, oak and pine woodlands, and coniferous forests [12,20,40,139]. It occurs in several types of chaparral including chamise, mixed, manzanita, and ceanothus chaparral. Chaparral vegetation is typically dense and has little to no understory except during the first year or two after fire .
Chamise chaparral and mixed chaparral: Chamise chaparral often occurs on south-facing slopes, while mixed chaparral with Eastwood's manzanita often occurs on north-facing slopes . Eastwood's manzanita frequently codominates with chamise [17,22,30,37,128]. In chamise chaparral on the San Bernardino National Forest, Eastwood's manzanita averaged about 17% less density and 12% less cover than that of chamise (mean density = 484 plants/acre (1,196/ha) versus 2,800 plants/acre (6,919/ha) and mean cover = 4.8% versus 39.4%, respectively) .
Eastwood's manzanita often dominates mixed chaparral above the chamise zone [37,91,128,146]: around 4,500 to 5,000 feet (1,400-1,500 m) elevation in southern California . Mixed chaparral in the Coast Ranges is composed of chamise, Eastwood's manzanita, bigberry manzanita, chaparral whitethorn, California scrub oak or coastal sage scrub oak, hoaryleaf ceanothus, and/or interior live oak . On the Cleveland and Los Padres National Forests, Eastwood's manzanita grows in and often dominates mixed chaparral, growing in association with chamise, coastal sage scrub oak, birchleaf mountain-mahogany, cupleaf ceanothus, California buckwheat, and chaparral yucca [17,35,42]. In the Sierra San Pedro Mártir of Baja California, Mexico, Eastwood's manzanita occurs in mixed chaparral with composition similar to that of mixed chaparral in southern California. Commonly associated species not previously mentioned include pointleaf manzanita, and sugar sumac .
Manzanita chaparral: Eastwood's manzanita dominates some manzanita chaparral [22,41,158]. On the San Bernardino National Forest, it codominates summit slopes with pinkbracted manzanita . In the Santa Ana Mountains on the Cleveland National Forest, nearly pure stands of Eastwood's manzanita occur above chamise-Eastwood's manzanita chaparral, starting around 3,200 feet (1,000 m) elevation. Density in the nearly pure Eastwood's manzanita stands averaged 3,736 stems/acre (9,232/ha). These stands are most common on gentle (10-30°), north-facing slopes on fine-textured shale-derived or clay soils. Chamise-Eastwood's manzanita communities occur mostly on south-facing slopes on granitic soils, and oak scrub is most common on steep (30-40°), north- and east-facing slopes .
Southern maritime chaparral: Eastwood's manzanita grows in and often dominates southern maritime chaparral [14,46]. Chamise is frequently codominant with Eastwood's manzanita in maritime chaparral . Del Mar manzanita is considered an indicator species of southern maritime chaparral  and dominates southern maritime chaparral in San Diego County . Associates of Eastwood's manzanita in maritime chaparral include barranca brush, California scrub oak, Encinitis false willow  and Torrey pine [41,46]. Maritime chaparral is usually <6 feet (2 m) tall. It is the rarest chaparral type due to urban development .
Montane chaparral: Eastwood's manzanita grows in and may dominate montane chaparral [17,43]. Montane chaparral often occurs on seral sites succeeding to conifer forests. On harsh sites, this may take many decades. Associated shrub species include birchleaf mountain-mahogany, bush chinquapin, and other manzanitas (e.g., Parry manzanita and pointleaf manzanita) .
Other chaparral types: Eastwood's manzanita associates in ceanothus-dominated stands with bigpod ceanothus, hairy ceanothus, woolyleaf ceanothus, chaparral whitethorn, and/or deerbrush, [42,95,124]. Eastwood's manzanita also occurs in redshank chaparral in southern California and in desert chaparral  in the Transverse Ranges, where it is associated with birchleaf mountain-mahogany, chaparral whitethorn, desert ceanothus, eastern Mojave buckwheat, and Sonoran scrub oak [42,95].
Oak scrub and oak woodlands: Eastwood's manzanita is a component of oak scrub and oak woodland communities. In oak scrub, it occurs in canyon live oak [17,43,48], California scrub oak, coastal sage scrub oak, and interior live oak communities [17,43,48,154]. Oak scrub sites are more mesic than chamise chaparral sites; typically, they occupy north-facing slopes or canyon bottoms [43,48]. On the San Bernardino National Forest, oak scrub with Eastwood's manzanita is most common on steep (30-40°), north- and east-facing slopes. California scrub oak-interior live oak/Eastwood's manzanita oak scrub communities occur in the Santa Ana Mountains . In oak woodlands, Eastwood's manzanita is an understory species in blue oak , canyon live oak [17,48], California black oak , and occasionally valley oak woodlands .
Conifer woodlands and mixed-conifer forests: In conifer belts, Eastwood's manzanita occurs in woodlands and mixed-conifer forests [11,72]. It is a component of the vegetation in Coulter pine [95,139], knobcone pine [48,139], Tecate cypress , bigcone Douglas-fir-canyon live oak , bristlecone fir , Jeffrey pine, ponderosa pine, and mixed-conifer woodlands and forests . On the San Bernardino National Forest, Coulter pine/Eastwood's manzanita communities are common on north- and northeast-facing slopes . Eastwood's manzanita also grows in Bishop pine-Bolander beach pine dwarf forests in Mendocino County . In the Siskiyou Mountains of southern Oregon, Eastwood's manzanita is an understory species in coast Douglas-fir/bigleaf maple forests .
Other communities: Eastwood's manzanita may finger into annual grassland, coastal sage scrub, and desert chaparral communities. Annual grassland borders low-elevation chaparral in northern California, while coastal sage scrub borders low-elevation chaparral on coastal exposures in southern California . Eastwood's manzanita dominates some coastal sage scrub-chaparral transition communities . Desert chaparral borders chaparral to the east. Desert chaparral has no homolog in northern California .See table A2 for a representative list of plant classifications in which Eastwood's manzanita occurs.
Eastwood's manzanita is an erect or mound-forming evergreen shrub, growing 3 to 10 feet (1-3 m) tall [20,27]. It has multiple stems arising from the basal burl . Sometimes the multiple stems are genetically distinct, resulting from grafting of seedlings that emerged from a fused seed propagule or a common animal horde . The stems and branches are crooked and rigid [121,141] and often bear ribbons of dead wood  (fig. 4). The bark is thin and shreddy [58,121,141].
All infrataxa of Eastwood's manzanita except Arctostaphylos glandulosa subsp. atumescens  form a large basal burl or lignotuber at the stem base [20,27,78]. In the San Gabriel Mountains, Eastwood's manzanita had basal burls that that were 3 to 6 feet (1-2 m) across . Jepson (1916) found basal burls of coastal populations in the Bay Area were completely buried. Basal burl diameters increased with each successive fire. Eventually, some were 10 feet (3 m) across, with highly irregular circular or crescent shapes .
The stems, leaves, inflorescences, and fruits of Eastwood's manzanita are sticky [1,23,58]. Leaves are alternate and sclerophyllous [20,121,141]. The inflorescence is a panicle  (fig. 2). The fruit is a mealy drupe [3,159] bearing stone seeds. For a single drupe, the stones may be free and separate or fused, depending on the infrataxon [3,27]. Fused stones form a single propagule .
|Figure 2—Eastwood's manzanita flowers. Image courtesy of Charles Webber ©California Academy of Sciences, used with permission.|
Eastwood's manzanita is a deep-rooted species. On sites with deep soil profiles, roots may extend >17 feet (5 m) down [45,54]. In the San Gabriel and San Bernardino mountains, lateral roots of Eastwood's manzanita were well branched and grew 3.0 inches (7.5 cm) or more in diameter and more than 17 feet deep. The lateral roots penetrated rock cracks that were apparently too tight for the roots of associated chamise to penetrate. Eastwood's manzanita had adventitious roots near the soil surface .
Eastwood's manzanita is long-lived for a chaparral species [42,95]: its maximum lifespan is estimated at >100 years . Growth rings can be used to age Eastwood's manzanita stands. This technique reveals stem age, not the age of the basal burl and roots, which are older . Hanes (1971) considered stands >50 years old "mature", and stands >60 years old "senescent" . On Mt. Tamalpais in Marin County, individuals in an Eastwood's manzanita population ranged from about 5 to 65 years old .
Pure Eastwood's manzanita stands tend to be dense and uniform in height, and ≥5.0 feet (1.5 m) tall when mature . In the Santa Ana Mountains, pure stands that had not burned for at least 25 years formed a dense, interwoven canopy of branches. The tallest individuals were 10 to 12 feet (3-4 m) tall. There were almost no woody seedlings or herbs in the understory . Above 3,000 feet (900 m) on the Cleveland National Forest, Eastwood's manzanita occurred in dense stands of mixed chaparral composed of mostly sprouting species. Stands older than ~40 years averaged about 8.0 feet (2.4 m) tall . In a study in the San Raphael Mountains, Zaca manzanita stands were nearly pure, with 50% to 100% canopy cover. In intershrub spaces, the soil surfaces were mostly bare, lacking seedlings of either Zaca manzanita or other plant species .Raunkiaer Life Form:
Vegetative Regeneration: Sprouting is the primary mode of regeneration for Eastwood's manzanita; it is considered a facultative seeder (or facultative sprouter) because it also establishes from seeds. Chaparral shrubs that do not sprout and establish only from seeds, such as bigberry manzanita, are considered obligate seeders [62,146]. Eastwood's manzanita sprouts from its basal burl after top-kill by fire (e.g., [11,20,22,23,53,57,78,141]) or mechanical injury, including mastication [13,115]. Sprouts are more common than seedlings after top-killing disturbances [64,146]. Multiple stems arise from the basal burl after top-kill .
Pollination and Breeding System: Eastwood's manzanita requires cross-pollination. Solitary bees and syrphid flies are among the pollinators. In the San Jacinto Mountains, Eastwood's manzanita produced fewer, smaller flowers and less sugary nectar than Pringle manzanita, an obligate seeder; hence, it attracted fewer pollinators .
Seed Production: Seed production in Eastwood's manzanita depends on the number of flower buds initiated the previous year . Drought may lower flower and seed set . Most sprouting chaparral species begin to set seed 3 to 5 years after fire or other top-killing events . Fruit and seed production of Eastwood's manzanita and other sprouting species are generally less than that of obligate seeders [62,75]. Over time, obligate seeders such as bigberry manzanita usually deposit more seeds in the community seed bank than sprouters such as Eastwood's manzanita . However, on a 23-year-old mixed-chaparral burn in Marin County, seed production and vegetative growth were similar for Eastwood's manzanita and bigberry manzanita .
Eastwood's manzanita can produce many flowers and seeds in favorable years. For a population in San Diego County, production averaged 5.6 seeds/fruit . Maximum mean seed production was 2,778 seeds/plant. Seed production was positively correlated with above-average precipitation the year prior (rs = 0.97, P < 0.05) . Not all seeds within a propagule may remain viable. For example, in three Eastwood's manzanita populations in coastal northern California, seed set of Eastwood's manzanita propagules was 50% to 62% of the propagules' ovule production. Diploid plants had higher rates of seed set than tetraploid plants .
Seed Dispersal: Most Eastwood's manzanita seeds disperse beneath or near the parent plant. Frugivorous animals [66,72,79,134], particularly coyotes and American black bears, disperse Eastwood's manzanita seeds longer distances [66,72,79].
Seed Banking: Eastwood's manzanita has a persistent, soil-stored seed bank. The seeds can remain viable in the soil for decades, so Eastwood's manzanita may establish from the soil seed bank on burned sites where it had not been a component of aboveground vegetation before fire . Its seed bank densities differ between sites and times-since-fire . A review reported Eastwood's manzanita seed bank densities of 8,422 (SE 1,575) seeds/m² in northern California, and from 3,038 (SE 731) seeds/m² to 4,116 (SE 982) seeds/m² in southern California . Over 10 years in San Diego County, Eastwood's manzanita contributed about 89.9 x 106 seeds/ha to the soil seedbed of an Eastwood's manzanita-bigberry manzanita community. Over that time, there was no significant change in the number of seeds in the soil seedbank of Eastwood's manzanita despite this high seed output . Rodents commonly deplete the seed bank of Eastwood's manzanita [62,81], and this likely hindered buildup of its seed bank on that site . Rates of seed predation were as high as 80% within 10 days of placement onto the soil surface . On Mt. Tamalpais, depletion due to seed predation was estimated at 14% over 11 months .
Although germination rates of soil-stored Eastwood's manzanita appear low compared to other chaparral species, seed production and seed bank numbers are high enough that this does not seem to limit Eastwood's manzanita establishment [64,81]. In a 2-year study on Mt. Tamalpais, Eastwood's manzanita seed bank numbers averaged 392.4 viable seeds/m2 the first year and 709.0 viable seeds/m2 the next .
Germination: Eastwood's manzanita seeds are dormant at ripening, having both a hard seed coat that requires scarification and embryo dormancy [64,159]. Fire [66,77,141,159], mechanical scarification, acid treatment , and/or exposure to charate leachate [64,66] break dormancy. Animal digestion results in scarification . Eastwood's manzanita seeds are considered refractory because in the field, intense heat shock or chemicals leached from charred wood induces germination . Keeley (1987) stated that germination of Eastwood's manzanita requires "a chemical cue from charred wood"  or intense heat , with most seeds remaining dormant until a fire breaks dormancy . Following scarification by fire and exposure to wet charate, overwinter stratification breaks embryo dormancy .
Soil-stored Eastwood's manzanita seeds show low viability in laboratory and field studies. In the laboratory, exposure to charate alone resulted in <5% germination . A combination of heat, light or dark treatments, and application of charate leachate to soil resulted in limited Eastwood's manzanita germination (2%-18%), while a combination of heat (180-212 oF (70-100 oC)), light or dark treatments, and application of distilled water resulted in 0% germination (P < 0.001). For a population in San Diego County, the percentage of filled (viable) seed in the soil ranged from 7% to 9% . On Mt. Tamalpais, viability of seeds in the soil seed bank averaged 7% .
Seedling Establishment and Plant Growth: Eastwood's manzanita requires open mineral soil to establish . In 12 chaparral sites across California, Eastwood's manzanita seedlings occurred on new burns, but few seedlings were present in chaparral 56 to 120 years old. Chaparral communities of other ages were not examined [67,68]. Fused seeds within a propagule may germinate together but over time, one seedling often becomes dominant while the others die . Seedling mortality can be high [5,146] (see Plant response to fire). Drought results in considerable mortality of Eastwood's manzanita seedlings, particularly for seedlings in desert chaparral .
Germinants and seedlings usually fail to establish in mature and old chaparral. In the Santa Ana Mountains, no Eastwood's manzanita seedlings were detected in chaparral that had not experienced fire for at least 40 years, although mature plants were present. Mortality of mature individuals was high in the stand, with dead Eastwood's manzanita plants averaging 297 plants/acre (734/ha) and live plants averaging 231 plants/acre (570/ha) .
Eastwood's manzanita sprouts grow quickly. On the Cleveland National Forest, Eastwood's manzanita sprouts on fuelbreaks averaged 2.0 feet (0. 6 m) tall 5 years after cutting . Wakimoto (1978) provides a model for predicting growth of Eastwood's manzanita based on age and current height. It was developed using data collected in chamise-redshanks-Eastwood's manzanita stands on the Cleveland National Forest .
Basal burls of manzanitas also develop quickly in young plants. Although basal burls grow larger with successive fires, fire is not required for their development .
Eastwood's manzanita continues to produce new stems as it matures, and one study suggests that growth rates are similar in mature and old stands. On 12 mature to old chaparral stands (56-120 years old) across California, Eastwood's manzanita plants continued to produce new sprouts from their aging basal burls . A study in 28-year-old and 90-year old mixed chaparral stands in San Diego County found growth of Eastwood's manzanita vegetative tissues was similar for the two stands (87.0 and 86.8 g oven dry weight/m2 of cover for the two stands, respectively). Fruit production slowed, but not substantially (62.6 and 55.8 oven dry weight/m2 of cover for the two stands, respectively) .
Subshrubs and herbaceous plants often have greatest cover in the first few years after a stand-replacing event such as fire or logging, with once-dominant shrubs such as Eastwood's manzanita having lower coverage. In chaparral, transition to the mid- to late-seral stages happens quickly (8-15 years). By then, shrubs that were dominant prior to the event occupy most of the available growing space (>80% canopy cover), with herbaceous species and subshrubs restricted to openings .
Within the chaparral belt, chaparral vegetation does not usually succeed to other vegetation types , likely because fires are too frequent for conifer establishment . Biswell (1974) noted that "chaparral is largely a fire-induced type with a remarkable capacity to persist with recurring fires" . However, montane chaparral often succeeds to pine woodland or forest . Initially, chaparral and montane chaparral have similar successional trajectories after a stand-replacing event. The early-seral stage of montane chaparral can have 0% to 70% shrub cover, with limited conifer seedling cover. However, the shrubs often become nurse plants for conifer regeneration . In mixed-conifer forests on the Blodgett Forest Research Station, Eastwood and other manzanita species developed dense canopies following stand-replacing fire or clearcutting . If fires reoccur within ~30 years, the montane chaparral might not succeed to conifer forest. This may occur on southerly slopes with shallow soils and on ridgetops, where fire behavior is often severe .
Eastwood's manzanita occurs in all stages of chaparral succession [11,42]. Fire has little effect on composition of chaparral dominated by species that both sprout and seed after fire, such as Eastwood's manzanita and chamise [11,29,79,147]: Sprouting shrubs usually dominate after fire if they dominated before . After 10 to 15 years growth, shrub foliar cover approaches prefire values and the canopy thins [108,123]. Within a few decades, Eastwood's manzanita and other chaparral shrubs recover their prefire height and density .
Over an approximately 70-year period, shrubs—including Eastwood Manzanita—remained dominant on sites with both frequent (≥2 fires in 91 years) and infrequent (0 or 1 fire in 91 years) fire in mixed chaparral in San Diego County. Repeat surveys in the 1930s and 2001 showed that neither trees nor annual grasses became dominant on the chaparral sites, even with infrequent fire. Cover and frequency of Eastwood's manzanita averaged 5% and 13%, respectively, in the 1930s and 7.5% and 17%, respectively, in 2001. On sites with infrequent fire, mean cover of sprouting shrubs, including Eastwood's manzanita, increased from 72% to 91%. On sites with frequent fire, it decreased from 87% to 80% .
Herbaceous species usually have greatest cover in chaparral in postfire years 1 or 2, then decrease in successive postfire years [28,80,146]. This may be true for nonnative invasive herbs as well as native herbs. In the Santa Monica Mountains, species richness of native and nonnative herbs increased during the first 2 years after fire, then gradually declined .Chaparral may convert to annual grassland with very frequent fire (fire intervals of <10-15 years), especially if annual grasses were present in the prefire plant community [21,72,77]. Litter of Eastwood's manzanita is allelopathic to annual grasses and other herbaceous species. In the absence of fire, compounds in Eastwood's manzanita litter apparently inhibit germination and establishment of groundlayer herbs beneath the Eastwood's manzanita canopy  (see Fire Management Considerations). However, fire intervals of <6 years may substantially reduce presence of Eastwood's manzanita and other sprouting shrubs .
Soil-stored Eastwood's manzanita seeds usually survive fire [11,62], although fire kills some Eastwood's manzanita seed stored in the seed bank . In particular, seeds in heavy duff may not survive .Postfire Regeneration Strategy:
|Figure 3—Eastwood's manzanita sprouting after fire in the Santa Ana Mountains. Photo ©2018 Ron Vanderhoff, used with permission.|
Plant response to fire: Eastwood's manzanita sprouts from its basal burl (lignotuber) after top-kill by fire (e.g., [11,22,23,42,53,57,72,77,79,141,144]) (fig. 3). The large basal burl and deep roots of this species favor sprouting compared to shallow-rooted species with small root crowns, which are usually nonsprouting . Eastwood's manzanita plants with small burls (i.e., young plants) or that lack burls (Arctostaphylos glandulosa subsp. atumescens) may not sprout after fire [54,79]. Sprouts emerge in postfire year 1 , soon after fire , and grow rapidly for the first 1 to 3 postfire years. Growth usually slows after that . However, in the San Bernardino Mountains, Eastwood's manzanita showed rapid growth for at least 15 postfire years .
In the San Gabriel Mountains, Eastwood's manzanita plants that had been repeatedly top-killed by fire had basal burls spreading 3 to 6 feet (1-2 m) across . After the Fern Canyon Fire in the San Bernardino Mountains, Eastwood's manzanita grew rapidly in the first 3 postfire years, with growth continuing more slowly for at least 15 postfire years (fig. 4). Sprout density of Eastwood's manzanita remained stable, averaging one plant/0.001 acre (0.2 plant/m2) over 15 years. Seedlings emerged at a density of 2 plants/0.001 acre (0.5 plant/m2)in postfire year 1, but they were not present on plots in postfire year 2 .
Figure 4—Eastwood's manzanita sprout height after the 1987 Fern Canyon Fire. Adapted from .
|Mean Eastwood's manzanita height (inches)
Jepson (1916) reported this response of Eastwood's manzanita :
|"After the Mt. Tamalpais chaparral fire of early July, 1913, sprouts began to appear within four weeks, and in two months made an abundant showing. Two of my students, Wieslander and Herbert, counted forty-eight sprouts in a square inch from the crown of an individual of this species" .|
Although sprouting is more common [64,146], Eastwood's manzanita also establishes from seed after fire [53,64,72,159], including pile burning . Eastwood's manzanita is deemed a postfire "facultative seeder" because unlike most manzanitas, it establishes from both seeds and sprouts after fire [41,72,77]. Fire cracks the hard seed coat , and leachate provides chemical cues that break seed dormancy  (see Germination). On one 4-year-old burn in southern California, 11% of Eastwood's manzanita plants were of seed origin and the rest were sprouts; on another 4-year-old burn, all Eastwood's manzanita plants were sprouts . Colonization can occur from off-site seed dispersed by parent plants adjacent to the burn  or from seed in the feces of frugivorous animals [66,72,79,134]. In a burned Tecate cypress community in San Diego County, Zedler (1977) noted both sprouting and postfire seedling establishment of Eastwood's manzanita. Although seed production and seed bank replenishment occurred in young and old stands, seedling establishment occurred only on new burns, in the first few postfire years. He attributed this to favorable nutrient and moisture conditions and sites available for germination and growth in early postfire environments .
Although Eastwood's manzanita seedlings may occur in large numbers after fire, seedling mortality is high [42,79,146], while sprout mortality is very low . In San Diego County, mortality of Eastwood's manzanita seedlings averaged 55% on a 1-year-old burn . On 1- and 2-year-old burns in the San Jacinto Mountains, researchers tallied large numbers of Eastwood's manzanita sprouts and seedlings, but they noted that "seedlings are suspected of seldom contributing to mature chaparral cover" due to high rates of mortality. Seedling density was 7.5% lower on the 2-year old burn compared to the 1-year-old burn (table 1). Eastwood's manzanita seedlings were most numerous on gentle slopes and level sites with a deep ash layer. Eastwood's manzanita sprouts averaged 4.9 feet (1.5 m) tall in postfire year 2. Eastwood's manzanita was the dominant shrub in postfire succession, averaging 8.0% cover on the 1-year-old burn and 25.3% cover on the 2-year-old burn .
|Table 1—Mean density (stems/acre) of Eastwood's manzanita sprouts and seedlings after two wildfires in Eastwood's manzanita-chamise chaparral in the San Jacinto Mountains. The control site had not burned for at least 42 years. Data were collected on 25 one-fiftieth acre (0.008 ha) quadrats .|
|Regeneration type||1-year-old burn||2-year-old burn||Unburned control|
Postfire recovery of Eastwood's manzanita is typically rapid [48,72]. On the Laguna-Morena Demonstration Area in San Diego County, rates of Eastwood's manzanita photosynthesis and water conductance—processes that lead to biomass accumulation and growth—were greater on burned plots than on hand-cleared or control plots, and were greater on hand-cleared plots than on control plots . Chaparral shrubs generally reach prefire height by postfire year 20, although regaining prefire cover and density takes longer. When new burns were compared to mature chaparral (>40 years old) in the Laguna Mountains of southern California, 85% of mature shrub cover was reached by postfire year 10. By postfire years 30 to 40, shrub cover was similar to that of mature chaparral . In chamise-Eastwood's manzanita chaparral on the Mt. Hamilton Range, Santa Clara County, cover of Eastwood's manzanita and chamise on burned sites was similar to that on adjacent unburned sites by postfire year 3 . After the September, 1970 Laguna Fire in San Diego County, a comparison of burned mixed chaparral to adjacent unburned mixed chaparral found early relative dominance of the burn by sprouting Eastwood's manzanita and chamise (table 2). Mortality of Eastwood's manzanita sprouts was very low; estimated at 7% and 10% on 1-year-old burned and unburned sites. In contrast, mortality of chamise was estimated at 38% to 50%, respectively (table 2). Individuals with small burls were most susceptible to fire kill. However, among the five dominant shrub species, Eastwood's manzanita had the lowest seedling establishment and highest seedling mortality  (table 3).
|Table 2—Postfire responses of mixed chaparral shrub species in stands burned in the Laguna Fire compared with shrubs in stands in adjacent unburned mixed chaparral. Data were collected in postfire year 1 .|
|coastal sage scrub oak||sprouting||5.0||2.5|
|all other shrubs or subshrub species||variable||0.9||18.0||11.2||7.8|
|Total basal area, all species
|not provided||463.9||26.3||not provided||not provided|
|Total density, all species
|not provided||not provided||not provided||12.0||41.4|
|aRelative dominance expressed as a percentage of total basal area.
bRelative density expressed as a percentage of total number of live stems of all species per unit area (stems/10 m2).
|Table 3—Shrub cover and seedling density in unburned chaparral compared to estimates of prefire shrub cover and shrub seedling density for each of the dominant species on the Laguna Burn. Transect and plot data are presented separately for bigberry manzanita and Eastwood's manzanita to show the relationship between seedling density and prefire cover. Unburned stands were sampled along 50-m transects. Adapted from .|
|total number||number alive||% dead||total number||number alive||% dead|
(20 × 30 m plots)
(20 × 30 m plots)
|aBasal burl area, live and dead, for the burl-forming species (Eastwood's manzanita and chamise) or basal area, live and dead, for the nonburl-forming species (bigberry manzanita and desert ceanothus). Seedlings were excluded. For the burn, this was used to estimate prefire population size.
bIn postfire year 1.
cConsisting of one or more seedlings arising from nearly the same point.
Recovery of mixed chaparral communities is typically rapid, and early-season fire may result in the most rapid postfire growth of Eastwood's manzanita. In Mendocino County, shrubs in mixed chaparral with Eastwood's manzanita recovered biomass rapidly. Total aboveground biomass averaged about 1,100 pounds/acre (1,200 kg/ha) in postfire year 1, and about 9,000 pounds/acre (10,100 kg/ha) in postfire year 6. Growth slowed by postfire year 6, and by postfire year 8, annual growth had "declined appreciably" . Based on vegetation surveys in the San Bernardino Mountains, Horton (1960) observed that postfire growth of chamise-Eastwood's manzanita stands was similar to that of chamise-ceanothus stands. He stated that both stands had ~45% crown cover in postfire year 10, ~75% in postfire year 40, and ~60% in postfire year 60. Crown heights ranged from 4 to 15 feet (1-5 m) at maturity . In chamise-manzanita stands north of Ukiah, California, burning and mastication treatments that occurred over different seasons reduced total vegetation cover by 90% to 100%. Mastication reduced shrub cover more than prescribed fire. Shrub cover was similar to that of the untreated control stand within 10 posttreatment years. Shrub cover was 1% to 2% less than of the untreated stand on plots treated with prescribed fire or spring mastication, while shrub cover on plots treated with fall mastication was 8% less than that of plots on the untreated stand. Spring prescribed fire was the only treatment where cover of Eastwood's manzanita was similar to that of the unburned stand, although this was not tested for significance. Treatments were conducted on sites that had not burned for >40 years. Cover of Eastwood's manzanita in these stands is shown in table 4 [155,156].
|Table 4—Percent Eastwood's manzanita covera before and after prescribed fire or mastication in chamise-manzanitab chaparral. Data are means (SE). Adapted from .|
|Fire||Prefire||Postfire year 1||Postfire year 2||Postfire year 3||Postfire year 4||Postfire year 10|
|Control||13(2)||not provided||not provided||not provided||not provided||not provided|
|Fall fire (Nov.)||11(3)||no data||7(5)||5(4)||11 (not calculated)||4(1)|
| Spring fire
|7(5)||7(not calculated)||15(3)||15(not calculated)||13(<1)||15(5)|
|Winter fire (Jan.)||17(5)||no data||10(2)||no data||10(4)||4(1)|
|Mastication||Preshred||Postshred year 1||Postshred year 2||Postshred year 3||Postshred year 4||Postshred year 10|
|Control||13(2)||not provided||not provided||not provided||not provided||not provided|
|Fall shred (Nov.)||13(2)||5(<1)||7(2)||8(3)||no data||8(4)|
| Spring shred
|8(3)||no data||5(4)||5(not calculated)||3(1)||4(1)|
|an = twenty-four 2-ha units; cover measured along fifteen 15-m transects/unit.
bManzanita species present in the community included Eastwood's manzanita, common manzanita, and Stanford's manzanita.
Few studies had been conducted on recovery of Eastwood's manzanita in oak or conifer woodlands as of 2020. In Tecate cypress stands in the Santa Ana Mountains, Eastwood's manzanita was not present in unburned stands. Its density averaged 2 plants/acre (6/ha) on 3-year-old burns and 68 plants/acre (168/ha) on 17-year-old burns. Its cover averaged 1.7% on 17-year-old burns (Armstong and Vogl, unpublished data cited in ). In knobcone pine woodlands, Eastwood's manzanita averaged 1,521 plants/acre (3,759/ha) and 1,314 plants/acre (3,246/ha) on unburned and burned plots, respectively. Cover averaged 21.4% and 18.3% on unburned and burned plots, respectively. Burned plots were sampled in either postfire year 4 or 16 .
The Research Project Summary "Response of vegetation to prescribed burning in a Jeffrey pine-California black oak woodland and a deergrass meadow at Cuyamaca Rancho State Park, California" provides information on the postfire response of Eastwood's manzanita and other plant species of that community.FUELS AND FIRE REGIMES
|Figure 4—Dead branchwood (ribbonwood) of Eastwood's manzanita. Photo ©Neal Kramer, used with permission.|
Moisture content of live chaparral fuels declines through spring, summer, and fall. It also varies with plant age. A study on the Stanislaus National Forest found fuel moisture of manzanitas peaked in late June to early July. Of course, this varies with year-to-year precipitation. Leaf moisture content of Eastwood's manzanita is lowest in late fall, before seasonal rains begin . Fuel moisture of Eastwood's manzanita plants may average 150% to 200% for new growth and 90% to 150% for old growth .
Eastwood manzanita accumulates live and dead standing fuels rapidly because it grows quickly after fire. . In chamise-redshanks-Eastwood's manzanita stands on the Cleveland National Forest, Eastwood's manzanita plants had substantial die-back of stems, which contributed to standing dead fuel loads as stands matured. Biomass of Eastwood's manzanita plants is comprised of more fine fuels than course fuels, which tends to enhance flammability. Over 65% of the biomass of all Eastwood's manzanita plants sampled was composed of tissues with diameters of ≤0.4 inch (1 cm). However, surface:volume ratio and calorie count of Eastwood's manzanita were less than that of chamise and redshanks . Wakimoto (1978) provides calorie count of live and dead Eastwood's manzanita fuels and models to predict aboveground biomass and rate of fuel build-up for Eastwood's manzanita. In his study, mixed chaparral with Eastwood's manzanita reached peak biomass around age 25, with 90% of this peak occurring at stand age 16 . Eisele (2015) provides data on live and deal fuels loads of 13- and 55-year-old chamise-Eastwood's manzanita-chaparral burns in San Diego County .
Eastwood's manzanita may be slower to ignite than species with thinner, nonsclerophylous leaves that are less able to retain moisture. Pickett et. al (2010) provide a model for ignition of Eastwood's manzanita leaves based on moisture content . Weise et al. (1991) provide information on the seasonal changes in moisture content of Eastwood's manzanita branches and foliage, and of carbon and particulate emissions of Eastwood's manzanita fuels. Their data were collected in southern California . Using fuel beds constructed in the laboratory, Weise et. al (2016) developed a model to predict fire spread success and rate of fire spread across Eastwood's manzanita fuel beds .
Chaparral dieback causes sudden increases in standing dead fuel loads. Sudden diebacks have been attributed to a fungus (Botryosphaeria dothidea) that infects Eastwood's manzanita and other shrubs weakened by extended drought .
Litter fuels accumulate slowly on the nutrient-poor, unproductive soils typical of chaparral . Litter deposition in pure Eastwood's manzanita stands can be considerable but decay rates rapid . In the Santa Ana Mountains, Wilson and Vogl (1965) noted that litter accumulated more rapidly in Eastwood's manzanita stands than in chamise stands, but subsequent decomposition of litter appeared more rapid in Eastwood's manzanita stands .
In chaparral, fires are nearly always carried in canopy fuels, with surface fuels playing little or no role in fire spread [72,73]. In a review of fire in chaparral, Keeley and Syphard (2018) wrote that "several lines of evidence suggest the primary determinant of fire size is the coincidence of ignitions and Santa Ana winds", not fuel buildup .
Fire Regimes: The mediterranean climate  and the flammability and continuity of fuels [97,113,157] make chaparral very susceptible to fire ignition and spread. Because California's chaparral region has a low frequency of lightning, most presettlement chaparral fires likely started as lightning-ignited fires in higher-elevation forests [8,11,70], although lightning-ignited fires likely started in chaparral in some years . It is unclear how often and when American Indians set fires in chaparral [8,11,85,86,120]. They mostly used fire in lower-elevation grasslands and higher-elevation woodlands [8,120].
Historically, California's fire season occurred during warm, dry periods from June through October, peaking at the end of the fire season [9,59,77,152]. Nearly rainless summers with high daytime temperatures and low humidity dry out the vegetation and soils, and high winds (Santa Ana or other foehn winds) blow from the interior deserts and valleys to the Pacific Ocean in late summer and fall [11,59]. Fire behavior in chaparral is strongly controlled by wind. Without strong winds, fire spread is driven by topography and the proportion of living and dead canopy biomass. Fires are nearly always active crown fires carried by living and dead fuels in the canopy, with surface fuels playing little or no role in fire spread [72,73].
Chaparral fires are severe  and stand replacing [71,93,146], typically consuming the shrub canopy, understory, and litter . Fires are particularly severe during high winds  and sometimes with long fire-free periods (>70 years), particularly on sites with heavy fuel loads. In the San Bernardino Mountains, California black oak-canyon live oak/ceanothus-Eastwood's manzanita montane chaparral burned at higher severity, and less often, on relatively wet sites compared to dry sites. High severity in the previous fire tended to reduce severity in the next fire. Time-since-fire tended to increase with increases in mean annual precipitation. Shrub cover was negatively associated with annual grass cover (cheatgrass, compact brome, red brome, ripgut brome, and wild oat), and shrubs tended to increase at the expense of nonnative annual grasses with time-since-fire (P < 0.05 for all variables) .
Mean historical fire interval in California chaparral is estimated at 55 years , with a range of 10 to 90 years [15,25,90]. Because fires consume fuels completely, fire recurrence at a site is reduced until sprouters like Eastwood's manzanita and obligate seeders like bigberry manzanita gain enough biomass to support fire continuity . Unburned stands over 50 years old might have been historically uncommon . However, Keeley and Zedler (1978) suggest that presettlement chaparral had both short and long fire-free periods, with southern coastal California remaining fire-free for up to a century . Historically, southern California chaparral landscapes are described as having many modest-size summer lightning-ignited fires that burned a relatively small portion of the landscape, and massive wind-driven fires once or twice a century (review by ). Some studies suggest that fire intervals of <6 years were rare  because stands <7 to 8 years old are unlikely to carry fire . However, other studies suggest that the probability of burning increases only moderately with time-since-fire, and fuels are limited only in certain areas. Rather, fire may spread through all age classes of fuels under high winds. Fuel age may be important in areas lacking high winds [99,100].
Sprouting chaparral species may withstand fire intervals as short as 10 years, which allows enough time for them to grow, produce seeds, and replenish the soil seedbank. Short fire intervals tend to favor facultative sprouting species such as Eastwood's manzanita over obligate seeding species such as bigberry manzanita [29,42,85,93]. Fire intervals of <10 years can substantially deplete occurrence of sprouting shrubs such as Eastwood's manzanita . Very frequent fire may convert chaparral to annual grasslands [70,132].
Urban development and associated human ignitions have apparently shortened intervals between chaparral fires, particularly in southern California. Human-ignited wildfires every 20 to 30 years throughout chaparral types are common . There is disagreement as to whether fire sizes have increased for chaparral in southern California under fire exclusion (see Fire regimes of California chaparral communities for details). Historically, fire sizes ranged from small [92,93,98] to large [72,77,84]. Because chaparral plant species rely on sprouting and a long-lived soil seedbank, they are not as affected by large fires as many forest plant species and usually recover quickly regardless of fire size .
Changes in the fire cycle have led to the state ranking of Del Mar manzanita as imperiled  (see Other Status).
For additional information about Fire Regimes of California chaparral, see Fire regimes of California chaparral communities.FIRE MANAGEMENT CONSIDERATIONS
Mule deer browse Eastwood's manzanita sprouts in postfire years 1 and 2, and may browse the seedlings "rather closely"  (see Importance to Wildlife and Livestock).
Nonnative Grasses: Eastwood's manzanita litter contains phytotoxins that retard germination of annual grasses. Chou and Mueller (1972, 1973) identified 12 allelopathic substances in Zaca manzanita leaf leachate. These substances were concentrated in newly burned soil after a wildfire in chamise-Zaca manzanita chaparral in San Barbara County. However, the substances leached out quickly after rainfall, providing a seedbed favorable for germination of brome grass and other nonnative annual grasses [18,19].
Mastication may result in increases of nonnative invasive herbs [13,155]. Ten years after treatments in chamise-manzanita chaparral north of Ukiah, masticated stands had higher cover of nonnative, invasive annual grasses than burned stands (P < 0.001). Stands that were treated (mastication or prescribed fire) in fall had greater mean density of nonnative plants than those treated in spring, and fall-burned plots had 10 to 40 times fewer nonnative annual grasses than masticated plots (P < 0.01). For spring treatments, there was ~10 times the cover of nonnative, invasive annual grasses with fire, and 100 times the cover with mastication compared to untreated plots. Annual grasses present included cheatgrass, red brome, soft brome, and wild oat .Seeding with nonnative grasses for postfire erosion control may slow recovery of Eastwood's manzanita and other native vegetation [5,39,104,107]. By rapidly creating a mat of fibrous roots at the soil surface, a stand of ryegrass can inhibit the cotyledons of shrub seedlings from pushing through the soil to light. This reduces the chances of shrub establishment [80,125,126]. Because chaparral seedlings establish primarily in the first 1 to 3 years after fire, future stand density and composition may be influenced by this early competition. After wildfire in the Ventura River Watershed on the Los Padres National Forest, postfire seeding with nonnative perennial ryegrass resulted in lower Eastwood's manzanita importance in seeded (relative importance value = 3%) compared to unseeded (relative importance value = 7%) plots .
Palatability and Nutritional Value: Eastwood's manzanita leaves and branches are unpalatable to most browsing animals [20,121,136], and overbrowsing of Eastwood's manzanita and other manzanitas indicates a rangeland in poor condition . Wildlife and domestic goats browse seedlings and new sprouts [20,121], and domestic goats may browse mature foliage lightly [36,121,141]. In mixed chaparral, browsing ungulates prefer oak scrub and chamise to Eastwood and other manzanita species [130,131]. On the Cleveland National Forest, domestic goats did not browse mature Eastwood's manzanita when free ranging, but they showed 80% utilization of leaves and small twigs when confined in fenced pastures at night [33,35]. After discking, they readily browsed sprouts  and 1-year-old seedlings . The rigid branches and often dense structure of Eastwood's manzanita stands impedes movement of large game animals and livestock through chaparral .
Arctostaphylos is Greek for "bear grape" [141,159]; manzanita is Spanish for "little apple" . As these names imply, the fruits are palatable to many frugivorous animals  including American black bears [20,141,159], mule deer, rabbits , rodents [74,121], wild turkeys, and grouse [20,141]. They are a staple for American black bears, coyotes , northern raccoons [20,137], and quail . Rodent predators of Eastwood's manzanita fruits include brush mice, deer mice, dusky-footed woodrats, and Heermann's kangaroo rats .
Seed predators generally prefer large manzanita seeds [74,110]. A review reported that seed bank predators removed bigberry manzanita seeds before Eastwood's manzanita seeds, and Eastwood's manzanita seeds before hoary manzanita seeds, which have the smallest seeds of the three manzanita species .
Protein and other nutrient levels are relatively low for Eastwood's manzanita browse. See these publications for information on nutritional content of Eastwood's manzanita browse: [21,136]. These publications provide information on seasonal variation in Eastwood's manzanita browse: [10,105].
Cover Value: Eastwood's manzanita often forms dense stands that provide good hiding, resting, and nesting sites for small birds and mammals. Horton (1960) reported that dusky-footed woodrats used Eastwood's manzanita as cover for their food caches . Open stands of Eastwood's manzanita provide good hiding and resting cover for mule deer .VALUE FOR RESTORATION OF DISTURBED SITES
Eastwood's manzanita fruits can be eaten raw or used to make jelly .
American Indians traditionally eat the fruits fresh and dried, and use them to make cider [7,20,141]. The seeds can be ground into meal [7,20,140]. Tea from the leaves was traditionally used as a wash to treat Pacific poison-oak rash .
OTHER MANAGEMENT CONSIDERATIONS
Eastwood's manzanita is allelopathic: it releases water-soluble toxins from its aboveground tissues and litter, inhibiting establishment and growth of herbaceous and woody species . Laboratory experiments have identified allelopathic substances in Zaca manzanita that likely inhibit germination and establishment of potentially competitive species . However, Eastwood's manzanita may facilitate establishment of conifers, particularly in montane chaparral (see Successional Status). In Marin County, planted coast Douglas-fir seedlings established in plots with Eastwood's manzanita but not in plots with chamise. Successful establishment was credited to ectomycorrhizal fungi associated with Eastwood's manzanita, but not with chamise .
|Table A1—Common and scientific names of plants mentioned in this Species Review. Links go to other FEIS Species Reviews.|
|Common name||Scientific name|
|brome grass||Bromus rigidus|
|compact brome||Bromus madritensis|
|perennial ryegrass||Lolium perenne subsp. perenne|
|red brome||Bromus rubens|
|ripgut brome||Bromus diandrus|
|soft brome||Bromus hordeaceus|
|wild oat||Avena fatua|
|Adams' manzanita||Arctostaphylos glandulosa subsp. adamsii|
|Campbell's manzanita||Arctostaphylos × campbelliae|
|barranca brush||Ceanothus verrucosus|
|bigberry manzanita||Arctostaphylos glauca|
|bigpod ceanothus||Ceanothus megacarpus|
|birchleaf mountain-mahogany||Cercocarpus montanus var. glaber|
|bush chinquapin||Chrysolepis sempervirens|
|California buckwheat||Eriogonum fasciculatum|
|California scrub oak||Quercus berberidifolia|
|chaparral yucca||Hesperoyucca whipplei|
|coastal sage scrub oak||Quercus dumosa|
|common manzanita||Arctostaphylos manzanita|
|cupleaf ceanothus||Ceanothus greggii var. perplexans|
|Eastwood's manzanita||Arctostaphylos glandulosa|
| subspecies with the same
|Arctostaphylos glandulosa subsp. atumescens|
|Arctostaphylos glandulosa subsp. erecta|
|Arctostaphylos glandulosa subsp. glandulosa|
|Arctostaphylos glandulosa subsp. glaucomollis|
|Arctostaphylos glandulosa subsp. leucophylla|
|Encinitis false willow||Baccharis vanessae|
|Campbell's manzanita||Arctostaphylos × campbelliae|
|chaparral whitethorn||Ceanothus leucodermis|
|Del Mar manzanita||Arctostaphylos glandulosa subsp. crassifolia|
|desert ceanothus||Ceanothus greggii|
|eastern Mojave buckwheat||Eriogonum fasciculatum|
|hairy ceanothus||Ceanothus oliganthus|
|hoaryleaf ceanothus||Ceanothus crassifolius|
|hoary manzanita||Ceanothus crassifolius|
|oak scrub||Quercus spp.|
|Pacific poison-oak||Toxicodendron diversilobum|
|Parry manzanita||Arctostaphylos parryana|
|pinkbracted manzanita||Arctostaphylos pringlei subsp. drupacea|
|pointleaf manzanita||Arctostaphylos pungens|
|Pringle manzanita||Arctostaphylos pringlei|
|Roof's manzanita||Arctostaphylos manzanita subsp. roofii|
|San Gabriel manzanita||Arctostaphylos gabrielensis|
|Sonoran scrub oak||Quercus turbinella|
|Stanford's manzanita||Arctostaphylos stanfordiana|
|sugar sumac||Rhus ovata|
|Transverse Range manzanita||Arctostaphylos glandulosa subsp. mollis|
|woolyleaf ceanothus||Ceanothus tomentosus|
|woolyleaf manzanita||Arctostaphylos tomentosa|
|Zaca manzanita||Arctostaphylos glandulosa subsp. zacaensis|
|bigcone Douglas-fir||Pseudotsuga macrocarpa|
|bigleaf maple||Acer macrophyllum|
|Bishop pine||Pinus muricata|
|blue oak||Quercus douglasii|
|Bolander beach pine||Pinus contorta var. bolanderi|
|bristlecone fir||Abies bracteata|
|canyon live oak||Quercus chrysolepis|
|coast Douglas-fir||Pseudotsuga menziesii var. menziesii|
|Coulter pine||Pinus coulteri|
|interior live oak||Quercus wislizeni|
|Jeffrey pine||Pinus jeffreyi|
|knobcone pine||Pinus attenuata|
|pinyon||Pinus, subsection Cembroides|
|ponderosa pine||Pinus ponderosa var. benthamiana,
P. ponderosa var. ponderosa
|Tecate cypress||Hesperocyparis forbesii|
|Torrey pine||Pinus torreyana|
|valley oak||Quercus lobata|
|Table A2—Representative plant community classifications in which Eastwood's manzanita occurs.|
|FRES21 Ponderosa pine|
|FRES 28 Western hardwoods|
|FRES 34 Chaparral-mountain shrub |
|Kuchler Plant Association|
|K002 Cedar-hemlock-Douglas-fir forest|
|K005 Mixed conifer forest|
|K009 Pine-cypress forest|
|K010 Ponderosa shrub forest|
|K029 California mixed evergreen forest|
|K030 California oakwoods|
|K034 Montane chaparral |
|SAF Cover Types|
|229 Pacific Douglas-fir|
|234 Douglas-fir-tanoak-Pacific madrone|
|244 Pacific ponderosa pine-Douglas-fir|
|245 Pacific ponderosa pine|
|246 California black oak|
|246 California black oak|
|247 Jeffrey pine|
|248 Knobcone pine|
|249 Canyon live oak|
|250 Blue oak-gray pine|
|255 California coast live oak |
|SRM (Rangeland) Cover Types|
|109 Ponderosa pine shrubland|
|201 Blue oak woodland|
|202 Coast live oak woodland|
|206 Chamise chaparral|
|207 Scrub oak mixed chaparral|
|208 Ceanothus mixed chaparral|
|209 Montane shrubland |
1. Alderman, DeForest C. 1979. Native edible fruits, nuts, vegetables, herbs, spices, and grasses of California: II. Small or bushy fruits. Leaflet 2278. Berkeley, CA: University of California, Division of Agricultural Sciences, Cooperative Extension. 26 p. 
2. Alexander, Earl B. 2011. Gabbro soils and plant distributions on them. Madrono. 58(2): 113-122. 
3. Baldwin, Bruce G.; Goldman, Douglas H.; Keil, David J.; Patterson, Robert; Rosatti, Thomas J.; Wilken, Dieter H., eds. 2012. The Jepson manual. Vascular plants of California, second edition. Berkeley, CA: University of California Press. 1568 p. 
4. Barbour, Michael G. 2007. Closed-cone pine and cypress forests. In: Barbour, Michael G.; Keeler-Wolf, Todd; Schoenherr, Allan A., eds. Terrestrial vegetation of California. Berkeley, CA: University of California Press: 296-312. 
5. Barro, Susan C.; Conard, Susan G. 1987. Use of ryegrass seeding as an emergency revegetation measure in chaparral ecosystems. Gen. Tech. Rep. PSW-102. Berkeley, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Forest and Range Experiment Station. 12 p. 
6. Bauer, Harry L. 1936. Moisture relations in the chaparral of the Santa Monica Mountains, California. Ecological Monographs. 6(3): 409-454. 
7. Bean, Lowell John; Saubel, Katherine Siva. 1972. Telmalpakh: Cahuilla Indian knowledge and usage of plants. Banning, CA: Malki Museum. 225 p. 
8. Bendix, Jacob. 2002. Pre-European fire in California chaparral. In: Vale, Thomas R., ed. Fire, native peoples, and the natural landscape. Washington, DC: Island Press: 269-294. 
9. Beyers, Jan L. 1998. Season of burn effects in southern California chaparral: Implications for management. In: Proceedings, 13th Conference on fire and forest meteorology; 1996 October 27-31; Lorne, Australia. Moran, WY: International Association of Wildland Fire: 389-398. 
10. Bissell, Harold D.; Strong, Helen. 1955. The crude protein variations in the browse diet of California deer. California Fish and Game. Sacramento, CA: California Department of Fish and Wildlife. 41(2): 145-155. 
11. Biswell, Harold H. 1974. Effects of fire on chaparral. In: Kozlowski, T. T.; Ahlgren, C. E., eds. Fire and ecosystems. New York: Academic Press: 321-364. 
12. Bolsinger, Charles L. 1989. Shrubs of California's chaparral, timberland, and woodland: Area, ownership, and stand characteristics. Res. Bull. PNW-RB-160. Portland, OR: U.S. Department of Agriculture, Forest Service, Pacific Northwest Experiment Station. 50 p. 
13. Brennan, Teresa J.; Keeley, Jon E. 2015. Effect of mastication and other mechanical treatments on fuel structure in chaparral. International Journal of Wildland Fire. 24(7): 949-963. 
14. Burge, Dylan O.; Parker, V. Thomas; Mulligan, Margaret; Valderamma, Cesar Garcia. 2018. Conservation genetics of the Endangered Del Mar manzanita (Arctostaphylos glandulosa subsp. crassifolia) based on RAD sequencing data. Madrono. 65(3): 117-130. 
15. Byrne, Roger; Michaelsen, Joel; Soutar, Andrew. 1977. Fossil charcoal as a measure of wildfire frequency in southern California: A preliminary analysis. In: Mooney, Harold A.; Conrad, C. Eugene, technical coordinators. Proceedings of the symposium on the environmental consequences of fire and fuel management in Mediterranean ecosystems; 1977 August 1-5; Palo Alto, CA. Gen. Tech. Rep. WO-3. Washington, DC: U.S. Department of Agriculture, Forest Service: 361-367. 
16. Calflora. 2020. The Calflora database: Information on California plants for education and conservation, [Online]. Berkeley, CA: Calflora (Producer). Available: http://www.calflora.org/. 
17. Cheng, Sheauchi, ed. 2004. Forest Service Research Natural Areas in California. Gen. Tech. Rep. PSW-GTR-188. Albany, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Research Station. 338 p. 
18. Chou, Chang-Hung. 1973. The effect of fire on the California chaparral vegetation. Botanical Bulletin of Academia Sinica. 14: 23-34. 
19. Chou, Chang-Hung; Muller, Cornelius H. 1972. Allelopathic mechanisms of Arctostaphylos glandulosa var. zacaensis. The American Midland Naturalist. 88(2): 324-347. 
20. Conrad, C. Eugene. 1987. Common shrubs of chaparral and associated ecosystems of southern California. Gen. Tech. Rep. PSW-99. Berkeley, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Forest and Range Experiment Station. 86 p. 
21. Dickens, S. J. M.; Allen, E. B. 2014. Exotic plant invasion alters chaparral ecosystem resistance and resilience pre- and post-wildfire. Biological Invasions. 16(5): 1119-1130. 
22. Dunne, Jim; Dennis, Ann; Bartolome, J. W.; Barrett, R. H. 1991. Chaparral response to a prescribed fire in the Mount Hamilton Range, Santa Clara County, California. Madrono. 38(1): 21-29. 
23. Eastwood, Alice. 1934. A revision of Arctostaphylos with key and descriptions. Leaflets of Western Botany. 1(11): 105-127. 
24. Eisele, Bob. 2015. An analysis of large chaparral fires in San Diego County, California. In: Keane, Robert E.; Jolly, Matt; Parsons, Russell; Riley, Karin, eds. Proceedings of the large wildland fires conference. 2014 May 19-23; Missoula, MT. Proceedings RMRS-P-73. Fort Collins, CO: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station: 77-89 [+ appendix]. 
25. Estes, Becky. 2016. Historic range of variability for chaparral in the Sierra Nevada and Southern Cascades, [Online]. In: Region 5; Plants & Animals; Ecology program documents, reports and publications; Natural range of variation of Sierra Nevada habitats. Vallejo, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Region (Producer). 44 p. Available: https://www.fs.usda.gov/detail/r5/plants-animals/?cid=stelprdb5434436 [2020, August 6]. 
26. Eyre, F. H., ed. 1980. Forest cover types of the United States and Canada. Washington, DC: Society of American Foresters. 148 p. 
27. Flora of North America Editorial Committee, eds. 2020. Flora of North America north of Mexico, [Online]. Flora of North America Association (Producer). Available: http://www.efloras.org/flora_page.aspx?flora_id=1. 
28. Florence, Melanie. 1987. Plant succession on prescribed burn sites in chamise chaparral. Rangelands. 9(3): 119-122. 
29. Franklin, Janet; Coulter, Charlotte L.; Rey, Sergio J. 2004. Change over 70 years in a southern California chaparral community related to fire history. Journal of Vegetation Science. 15(5): 701-710. 
30. Fried, Jeremy S.; Bolsinger, Charles L.; Beardsley, Debby. 2004. Chaparral in southern and central coastal California in the mid-1990s: Area, ownership, condition, and change. Resource Bulletin PNW-RB-240. Portland, OR: U.S. Department of Agriculture, Forest Service, Pacific Northwest Research Station. 86 p. 
31. Fulton, Robert E.; Carpenter, F. Lynn. 1979. Pollination, reproduction, and fire in California Arctostaphylos. Oecologia. 38(2): 147-157. 
32. Garrison, George A.; Bjugstad, Ardell J.; Duncan, Don A.; Lewis, Mont E.; Smith, Dixie R. 1977. Vegetation and environmental features of forest and range ecosystems. Agric. Handb. 475. Washington, DC: U.S. Department of Agriculture, Forest Service. 68 p. 
33. Green, Lisle R. 1980. Goat browsing to control brush regrowth on fuelbreaks in southern California. In: Proceedings, Society for Range Management, 33rd annual meeting; 1980 February 11-14; San Diego, CA. Denver, CO: Society for Range Management: 23. 
34. Green, Lisle R. 1981. Burning by prescription in chaparral. Gen. Tech. Rep. PSW-51. Berkeley, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Forest and Range Experiment Station. 36 p. 
35. Green, Lisle R.; Hughes, Catherine L.; Graves, Walter L. 1979. Goat control of brush re-growth on southern California fuelbreaks. Rangelands. 1(3): 117-119. 
36. Green, Lisle R.; Newell, Leonard A. 1982. Using goats to control brush regrowth on fuelbreaks. Gen. Tech. Rep. PSW-59. Berkeley, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Forest and Range Experiment Station. 13 p. 
37. Griffin, James R. 1975. Plants of the highest Santa Lucia and Diablo Range peaks, California. Res. Pap. PSW-110. Berkeley, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Forest and Range Experiment Station. 50 p. 
38. Griffin, James R. 1978. The Marble-Cone fire ten months later. Fremontia. 6(2): 8-14. 
39. Griffin, James R. 1982. Pine seedlings, native ground cover, and Lolium multiflorum on the Marble-Cone burn, Santa Lucia Range, California. Madrono. 29(3): 177-188. 
40. Guo, Qinfeng. 2017. Temporal changes in native-exotic richness correlations during early post-fire succession. Acta Oecologica. 80: 47-50. 
41. Halsey, Richard W. 2005. Chaparral, California's unknown wilderness. In: Fire, chaparral, and survival in southern California. San Diego, CA: Sunbelt Publications: 1-30. 
42. Hanes, Ted L. 1971. Succession after fire in the chaparral of southern California. Ecological Monographs. 41(1): 27-52. 
43. Hanes, Ted L. 1976. Vegetation types of the San Gabriel Mountains. In: Latting, June, ed. Symposium proceedings: Plant communities of southern California; 1974 May 4; Fullerton, CA. Special Publication No. 2. Berkeley, CA: California Native Plant Society: 65-76. 
44. Hastings, Steve J.; Oechel, Walter C.; Sionit, Nasser. 1989. Water relations and photosynthesis of chaparral resprouts and seedlings following fire and hand clearing. In: Keeley, Sterling C., ed. The California chaparral: Paradigms reexamined. No. 34: Science Series. Los Angeles, CA: Natural History Museum of Los Angeles County: 107-113. 
45. Hellmers, H.; Horton, J. S.; Juhren, G.; O'Keefe, J. 1955. Root systems of some chaparral plants in southern California. Ecology. 36(4): 667-678. 
46. Holland, Robert F. 1986. Preliminary descriptions of the terrestrial natural communities of California. Sacramento, CA: California Department of Fish and Game. 156 p. 
47. Horton, J. S.; Kraebel, C. J. 1955. Development of vegetation after fire in the chamise chaparral of southern California. Ecology. 36(2): 244-262. 
48. Horton, Jerome S. 1960. Vegetation types of the San Bernardino Mountains. Tech. Pap. No. 44. Berkeley, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Forest and Range Experiment Station. 29 p. 
49. Horton, Thomas R.; Bruns, Thomas D.; Parker, V. Thomas. 1999. Ectomycorrhizal fungi associated with Arctostaphylos contribute to Pseudotsuga menziesii establishment. Canadian Journal of Botany. 77(1): 93-102. 
50. Jacobsen, Anna L.; Pratt, R. Brandon. 2013. Vulnerability to cavitation of central California Arctostaphylos (Ericaceae): A new analysis. Oecologia. 171(2): 329-334. 
51. Jacobsen, Anna L.; Pratt, R. Brandon; Davis, Stephen D.; Ewers, Frank W. 2008. Comparative community physiology: Nonconvergence in water relations among three semi-arid shrub communities. New Phytologist. 180(1): 100-113. 
52. Jacobsen, Anna L.; Pratt, R. Brandon; Ewers, Frank W.; Davis, Stephen D. 2007. Cavitation resistance among 26 chaparral species of southern California. Ecological Monographs. 77(1): 99-115. 
53. James, Susanne Marie. 1983. Lignotubers and vegetative regeneration of Arctostaphylos in the California chaparral: Anatomy, morphology and ecological significance. Riverside, CA: University of California. 133 p. Dissertation. 
54. James, Susanne. 1984. Lignotubers and burls: Their structure, function and ecological significance in Mediterranean ecosystems. Botanical Review. 50(3): 225-266. 
55. Jefferson, Lara Vanessa; Pennacchio, Marcello; Havens, Kayri. 2014. Ecology of plant-derived smoke: Its use in seed germination. New York: Oxford University Press. 316 p. 
56. Jen, Coty N.; Liang, Yutong; Hatch, Lindsay E.; Kreisberg, Nathan M.; Stamatis, Christos; Kristensen, Kasper; Battles, John J.; Stephens, Scott L.; York, Robert A.; Barsanti, Kelley C.; Goldstein, Allen H. 2018. High hydroquinone emissions from burning manzanita. Environmental Science and Technology Letters. 5: 309-314. 
57. Jepson, Willis L. 1916. Regeneration in Manzanita. Madrono. 1(1): 3-11. 
58. Jepson, Willis Linn. 1923. Revision of the Californian species of Arctostaphylos. Madrono. 1(5): 87-96. 
59. Jin, Yufang; Goulden, Michael L.; Faivre, Nicolas; Veraverbeke, Sander; Fengpeng, Sun; Hall, Alex; Hand, Michael S.; Hook, Simon; Randerson, James T. 2015. Identification of two distinct fire regimes in southern California: Implications for economic impact and future change. Environmental Research Letters. 10(9): 1748-9326. 
60. Kartesz, J. T. The Biota of North America Program (BONAP). 2015. Taxonomic Data Center, [Online]. Chapel Hill, NC: The Biota of North America Program (Producer). Available: http://bonap.net/tdc [Maps generated from Kartesz, J. T. 2010. Floristic synthesis of North America, Version 1.0. Biota of North America Program (BONAP). [in press]. 
61. Keeley, J. E.; Brooks, A.; Bird, T.; Cory, S.; Parker, H.; Usinger, E. 1986. Demographic structure of chaparral under extended fire-free conditions. In: DeVries, Johannes J., ed. Proceedings of the chaparral ecosystems research conference; 1985 May 16-17; Santa Barbara, CA. Report No. 2. Davis, CA: University of California, California Water Resources Center: 133-137. 
62. Keeley, Jon E. 1977. Seed production, seed populations in soil, and seedling production after fire for two congeneric pairs of sprouting and nonsprouting chaparral shrubs. Ecology. 58(4): 820-829. 
63. Keeley, Jon E. 1982. Distribution of lightning- and man-caused wildfires in California. In: Conrad, C. Eugene; Oechel, Walter C., tech. coords. Proceedings of the symposium on dynamics and management of Mediterranean-type ecosystems; 1981 June 22-26; San Diego, CA. Gen. Tech. Rep. PSW-58. Berkeley, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Forest and Range Experiment Station: 431-437. 
64. Keeley, Jon E. 1987. Role of fire in seed germination of woody taxa in California chaparral. Ecology. 68(2): 434-443. 
65. Keeley, Jon E. 1987. Ten years of change in seed banks of the chaparral shrubs, Arctostaphylos glauca and A. glandulosa. The American Midland Naturalist. 117(2): 446-448. 
66. Keeley, Jon E. 1991. Seed germination and life history syndromes in the California chaparral. The Botanical Review. 57(2): 81-116. 
67. Keeley, Jon E. 1992. Demographic structure of California chaparral in the long-term absence of fire. Vegetation Science. 3(1): 79-90. 
68. Keeley, Jon E. 1992. Recruitment of seedlings and vegetative sprouts in unburned chaparral. Ecology. 73(4): 1194-1208. 
69. Keeley, Jon E. 1993. Utility of growth rings in the age determination of chaparral shrubs. Madrono. 40(1): 1-14. 
70. Keeley, Jon E. 2002. Native American impacts on fire regimes of the California coastal ranges. Journal of Biogeography. 29(3): 303-320. 
71. Keeley, Jon E.; Brennan, Teresa; Pfaff, Anne H. 2008. Fire severity and ecosystem responses following crown fires in California shrublands. Ecological Applications. 18(6): 1530-1546. 
72. Keeley, Jon E.; Davis, Frank W. 2007. Chaparral. In: Barbour, Michael G.; Keeler-Wolf, Todd; Schoenherr, Allan A., eds. Terrestrial vegetation of California. Berkeley, CA: University of California Press: 339-366. 
73. Keeley, Jon E.; Fotheringham, C. J. 2003. Historical fire regime in southern California. Fire Management Today. 63(1): 8-9. 
74. Keeley, Jon E.; Hays, Robert L. 1976. Differential seed predation on two species of Arctostaphylos (Ericaceae). Oecologia. 24: 71-81. 
75. Keeley, Jon E.; Keeley, Sterling C. 1977. Energy allocation patterns of a sprouting and a nonsprouting species of Arctostaphylos in the California chaparral. The American Midland Naturalist. 98(1): 1-10. 
76. Keeley, Jon E.; Keeley, Sterling C. 1981. Post-fire regeneration of southern California chaparral. American Journal of Botany. 68(4): 524-530. 
77. Keeley, Jon E.; Syphard, Alexandra D. 2018. South Coast bioregion. In: van Wagtendonk, Jan W.; Sugihara, Neil G.; Stephens, Scott L.; Thode, Andrea E.; Shaffer, Kevin E.; Fites-Kaufman, Jo Ann, eds. Fire in California's ecosystems. 2nd ed. Oakland, CA: University of California Press: 319-351. 
78. Keeley, Jon E.; Vasey, Michael C.; Parker, V. Thomas. 2007. Subspecific variation in the widespread burl-forming Arctostaphylos glandulosa. Madrono. 54(1): 42-62. 
79. Keeley, Jon E.; Zedler, Paul H. 1978. Reproduction of chaparral shrubs after fire: A comparison of sprouting and seeding strategies. The American Midland Naturalist. 99(1): 142-161. 
80. Keeley, Sterling C.; Keeley, Jon E.; Hutchinson, Steve M.; Johnson, Albert W. 1981. Postfire succession of the herbaceous flora in southern California chaparral. Ecology. 62(6): 1608-1621. 
81. Kelly, Victoria R.; Parker, V. Thomas. 1990. Seed bank survival and dynamics in sprouting and nonsprouting Arctostaphylos species. The American Midland Naturalist. 124(1): 114-123. 
82. Kelly, Victoria R.; Parker, V. Thomas. 1991. Percentage seed set, sprouting habit and ploidy level in Arctostaphylos (Ericaceae). Madrono. 38(4): 227-232. 
83. Kuchler, A. W. 1964. Manual to accompany the map of potential vegetation of the conterminous United States. Special Publication No. 36. New York: American Geographical Society. 166 p. 
84. Leiberg, John B. 1900. The San Gabriel Forest Reserve. In: Walcott, C. D.; Gannett, Henry. Twentieth annual report of the United States Geological Survey to the Secretary of the Interior, 1898-1899. Washington, DC: U.S. Government Printing Office: 411-428. 
85. Lewis, Henry T. 1973. Patterns of Indian burning in California: Ecology and ethnohistory. Ballena Press Anthropological Papers No. 1. Ramona, CA: Ballena Press. 101 p. 
86. Lewis, Henry T. 1993. Patterns of Indian burning in California: Ecology and ethnohistory. In: Blackburn, Thomas C.; Anderson, Kat, eds. Before the wilderness: Environmental management by native Californians. Menlo Park, CA: Ballena Press: 55-116. 
87. Li, Jing; Mahalingam, Shankar; Weise, David R. 2017. Experimental investigation of fire propagation in single live shrubs. International Journal of Wildland Fire. 26(1): 58-70. 
88. Martin, Bradford D. 1981. Vegetation responses to prescribed burning in a mixed-conifer woodland, Cuyamaca Rancho State Park, California. Loma Linda, CA: Loma Linda University. 112 p. Thesis. 
89. Martin, Bradford D. 1982. Vegetation responses to prescribed burning in Cuyamaca Rancho State Park, California. In: Conrad, C. Eugene; Oechel, Walter C., technical coordinators. Proceedings of the symposium on dynamics and management of Mediterranean-type ecosystems; 1981 June 22-26; San Diego, CA. Gen. Tech. Rep. PSW-58. Berkeley, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Forest and Range Experiment Station: 617. 
90. McPherson, James K.; Muller, Cornelius H. 1969. Allelopathic effects of Adenostoma fasciculatum, "chamise", in the California chaparral. Ecological Monographs. 39(2): 177-198. 
91. Miller, Erwin H., Jr. 1947. Growth and environmental conditions in southern California chaparral. The American Midland Naturalist. 37(2): 379-420. 
92. Minnich, Richard A. 1987. Fire behavior in southern California chaparral before fire control: The Mount Wilson burns at the turn of the century. Annals of the Association of American Geographers. 77(4): 599-618. 
93. Minnich, Richard A. 1988. The biogeography of fire in the San Bernardino Mountains of California: A historical study. University of California publications in geography: Volume 28. Berkeley, CA: University of California Press. 161 p. 
94. Minnich, Richard A. 1989. Chaparral fire history in San Diego County and adjacent northern Baja California. In: Keeley, Sterling C., ed. The California chaparral: Paradigms reexamined. No. 34: Science Series. Los Angeles, CA: Natural History Museum of Los Angeles County: 37-47. 
95. Minnich, Richard A. 2007. Southern California conifer forests. In: Barbour, Michael G.; Keeler-Wolf, Todd; Schoenherr, Allan A., eds. Terrestrial vegetation of California. Berkeley, CA: University of California Press: 502-538. 
96. Minnich, Richard A.; Bahre, Conrad J. 1995. Wildland fire and chaparral succession along the California-Baja California boundary. International Journal of Wildland Fire. 5(1): 13-24. 
97. Minnich, Richard A.; Dezzani, Raymond J. 1991. Suppression, fire behavior, and fire magnitudes in Californian chaparral at the urban/wildland interface. Report No. 75. Berkeley, CA: University of California, Water Resources Center. 16 p. 
98. Minnich, Richard A.; Franco-Vizcaino, Ernesto. 1997. Mediterranean vegetation of northern Baja California. Fremontia. 25(3): 3-12. 
99. Moritz, Max A. 2003. Spatiotemporal analysis of controls on shrubland fire regimes: age dependency and fire hazard. Ecology. 84(2): 351-361. 
100. Moritz, Max A.; Keeley, Jon E.; Johnson, Edward A.; Schaffner, Andrew A. 2004. Testing a basic assumption of shrubland fire management: How important is fuel age? Frontiers in Ecology and the Environment. 2(2): 67-72. 
101. Muller, Cornelius H.; Hanawalt, Ronald B.; McPherson, James K. 1968. Allelopathic control of herb growth in the fire cycle of California chaparral. Bulletin of the Torrey Botanical Club. 95(3): 225-231. 
102. Munz, Philip A.; Keck, David D. 1973. A California flora and supplement. Berkeley, CA: University of California Press. 1905 p. 
103. Murphy, Alfred H.; Leonard, Oliver A.; Torell, Donald T. 1975. Chaparral shrub control as influenced by grazing, herbicides and fire. Down to Earth. 31(3): 1-8. 
104. Nadkarni, Nalini M.; Odion, Dennis C. 1986. Effects of seeding an exotic grass Lolium multiflorum on native seedling regeneration following fire in a chaparral community. In: DeVries, Johannes J., ed. Proceedings of the chaparral ecosystems research conference; 1985 May 16-17; Santa Barbara, CA. Report No. 2. Davis, CA: University of California, California Water Resources Center: 115-121. 
105. Narvaez, N.; Brosh, A.; Pittroff, W. 2010. Seasonal dynamics of nutritional quality of California chaparral species. Animal Feed Science and Technology. 158(1-2): 44-56. 
106. NatureServe. 2019. NatureServe Explorer: An online encyclopedia of life, [Online]. Version 7.1. Arlington, VA: NatureServe (Producer). Available: http://explorer.natureserve.org/. 
107. O'Leary, John F. 1995. Potential impacts of emergency seeding on cover and diversity patterns of Californian shrubland communities. In: Keeley, Jon F.; Scott, Tom, eds. Brushfires in California: Ecology and resource management: Proceedings; 1994 May 6-7; Irvine, CA. Fairfield, WA: International Association of Wildland Fire: 141-148. 
108. O'Leary, John Francis. 1984. Environmental factors influencing postburn vegetation in a southern California shrubland. Los Angeles, CA: University of California. 92 p. Dissertation. 
109. Oechel, W. C.; Hastings, S. J. 1983. The effects of fire on photosynthesis in chaparral resprouts. In: Kruger, F. J.; Mitchell, D. T.; Jarvis, J. U. M., eds. Mediterranean-type ecosystems: The role of nutrients. New York: Springer-Verlag: 274-285. 
110. Parker, V. Thomas; Kelly, Victoria R. 1989. Seed banks in California chaparral and other Mediterranean climate shrublands. In: Leck, Mary Alessio; Parker, V. Thomas; Simpson, Robert L., eds. Ecology of soil seed banks. San Diego, CA: Academic Press: 231-255. 
111. Parker, V. Thomas; Vasey, Michael C. 2016. Two new subspecies of Arctostaphylos (Ericaceae) from California and implications for understanding diversification in this genus. Madrono. 63(3): 283-291. 
112. Parker, Virgil Thomas. 1984. Correlation of physiological divergence with reproductive mode in chaparral shrubs. Madrono. 31(4): 231-242. 
113. Philpot, Charles W. 1977. Vegetative features as determinants of fire frequency and intensity. In: Mooney, Harold A.; Conrad, C. Eugene, technical coordinators. Proceedings of the symposium on the environmental consequences of fire and fuel management in Mediterranean ecosystems; 1977 August 1-5; Palo Alto, CA. Gen. Tech. Rep. WO-3. Washington, DC: U.S. Department of Agriculture, Forest Service: 12-16. 
114. Pickett, Brent M.; Isackson, Carl; Wunder, Rebecca; Fletcher, Thomas H.; Butler, Bret W.; Weise, David R. 2010. Experimental measurements during combustion of moist individual foliage samples. International Journal of Wildland Fire. 19(2): 153-162. 
115. Potts, Jennifer B.; Marino, Eva; Stephens, Scott L. 2010. Chaparral shrub recovery after fuel reduction: A comparison of prescribed fire and mastication techniques. Plant Ecology. 210(2): 303-315. 
116. Raunkiaer, C. 1934. The life forms of plants and statistical plant geography. Oxford, England: Clarendon Press. 632 p. 
117. Roberts, Stephen W.; Bowman, William D. 1984. Osmotic and turgor relations in selected chaparral shrub species. Tasks for Vegetation Science. 13: 77-84. 
118. Rosario, John A.; Lathrop, Earl W. 1974. Comparison of vegetation structure and composition in modified and natural chaparral. Journal of Range Management. 27(4): 310-312. 
119. Rundel, Philip W. 1981. Structural and chemical components of flammability. In: Mooney, H. A.; Bonnicksen, T. M.; Christensen, N. L.; Lotan, J. E.; Reiners, W. A., tech. coords. Fire regimes and ecosystem properties: Proceedings of the conference; 1978 December 11-15; Honolulu, HI. Gen. Tech. Rep. WO-26. Washington, DC: U.S. Department of Agriculture, Forest Service: 183-207. 
120. Sampson, Arthur W. 1944. Plant succession on burned chaparral lands in northern California. Bulletin. 685. Berkeley, CA: University of California, College of Agriculture, Agricultural Experiment Station. 144 p. 
121. Sampson, Arthur W.; Jespersen, Beryl S. 1963. California range brushlands and browse plants. Berkeley, CA: University of California, Division of Agricultural Sciences; California Agricultural Experiment Station, Extension Service. 162 p. 
122. Sarr, D. A.; Hibbs, D. E. 2007. Woody riparian plant distributions in western Oregon, USA: Comparing landscape and local scale factors. Plant Ecology. 190(2): 291-311. 
123. Schlesinger, William H.; Gill, David S. 1978. Demographic studies of the chaparral shrub, Ceanothus megacarpus, in the Santa Ynez Mountains, California. Ecology. 59(6): 1256-1263. 
124. Schlesinger, William H.; Gray, John T.; Gill, David S.; Mahall, Bruce E. 1982. Ceanothus megacarpus chaparral: A synthesis of ecosystem processes during development and annual growth. Botanical Review. 48(1): 71-117. 
125. Schultz, A. M.; Biswell, H. H. 1952. Competition between grasses reseeded on burned brushlands in California. Journal of Range Management. 5(5): 338-345. 
126. Schultz, A. M.; Launchbaugh, J. L.; Biswell, H. H. 1955. Relationship between grass density and brush seedling survival. Ecology. 36(2): 226-238. 
127. Schwilk, Dylan W. 2003. Flammability is a niche construction trait: Canopy architecture affects fire intensity. The American Naturalist. 162(6): 725-733. 
128. Sharsmith, Helen K. 1945. Flora of the Mount Hamilton range of California (a taxonomic study and floristic analysis of the vascular plants). The American Midland Naturalist. 34(2): 289-367. 
129. Shiflet, Thomas N., ed. 1994. Rangeland cover types of the United States. Denver, CO: Society for Range Management. 152 p. 
130. Sidahmed, Ahmed E.; Morris, J. G.; Radosevich, S. R. 1981. Summer diet of Spanish goats grazing chaparral. Journal of Range Management. 34(1): 33-35. 
131. Sidahmed, Ahmed E.; Morris, James G.; Radosevich, Steven; Koong, Ling J. 1982. Seasonal changes in chaparral composition and intake by Spanish goats. In: Conrad, C. Eugene; Oechel, Walter C., technical coordinators. Proceedings of the symposium on dynamics and management of Mediterranean-type ecosystems; 1981 June 22-26; San Diego, CA. Gen. Tech. Rep. PSW-58. Berkeley, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Forest and Range Experiment Station: 258-263. 
132. Smith, April G.; Newingham, Beth A.; Hudak, Andrew T.; Bright, Benjamin C. 2019. Got shrubs? Precipitation mediates long-term shrub and introduced grass dynamics in chaparral communities after fire. Fire Ecology. 15(12): 16 p. 
133. Stickney, Peter F. 1989. Seral origin of species comprising secondary plant succession in northern Rocky Mountain forests. FEIS workshop: Postfire regeneration. Unpublished draft on file at: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station, Fire Sciences Laboratory, Missoula, MT. 10 p. 
134. Syphard, Alexandra D.; Franklin, Janet. 2010. Species traits affect the performance of species distribution models for plants in southern California. Journal of Vegetation Science. 21(1): 177-189. 
135. Taber, Richard D. 1953. Studies of black-tailed deer reproduction on three chaparral cover types. California Fish and Game. 39(2): 177-186. 
136. Taber, Richard D.; Dasmann, Raymond F. 1958. The black-tailed deer of the chaparral: Its life history and management in the North Coast Range of California. Game Bulletin No. 8. Sacramento, CA: State of California, Department of Fish and Game, Game Management Branch. 166 p. 
137. Tevis, Lloyd, Jr. 1947. Summer activities of California raccoons. Journal of Mammalogy. 28(4): 323-332. 
138. The Jepson Herbarium. 2020. Jepson online interchange for California floristics, [Online]. In: Jepson Flora Project. Berkeley, CA: University of California, The University and Jepson Herbaria (Producers). Available: http://ucjeps.berkeley.edu/interchange.html 
139. Thomas, Timothy W. 1987. Population structure of the valley oak in the Santa Monica Mountains National Recreation Area. In: Plumb, Timothy R.; Pillsbury, Norman H., technical coordinators. Proceedings of the symposium on multiple-use management of California's hardwood resources; 1986 November 12-14; San Luis Obispo, CA. Gen. Tech. Rep. PSW-100. Berkeley, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Forest and Range Experiment Station: 335-340. 
140. Timbrook, Jan. 1990. Ethnobotany of Chumash Indians, California, based on collections by John P. Harrington. Economic Botany. 44(2): 236-253. 
141. USDA, Forest Service. 1937. Range plant handbook. Washington, DC: U.S. Department of Agriculture, Forest Service. 532 p. 
142. USDA, NRCS. 2020. The PLANTS Database, [Online]. Greensboro, NC: U.S. Department of Agriculture, Natural Resources Conservation Service, National Plant Data Team (Producer). Available: https://plants.usda.gov/. 
143. USDI, Fish and Wildlife Service. 2020. Endangered Species Program, [Online]. U.S. Department of the Interior, Fish and Wildlife Service (Producer). Available: https://www.fws.gov/endangered/. 
144. Vasey, Michael; Parker, V. Thomas. 2008. A newly described species of Arctostaphylos (Ericaceae) from the central California coast. Madrono. 55(3): 238-243. 
145. Vogl, Richard J. 1973. Ecology of knobcone pine in the Santa Ana Mountains, California. Ecological Monographs. 43: 125-143. 
146. Vogl, Richard J.; Schorr, Paul K. 1972. Fire and manzanita chaparral in the San Jacinto Mountains, California. Ecology. 53(6): 1179-1188. 
147. Wakimoto, Ronald H. 1978. Responses of southern California brushland vegetation to fuel manipulation. Berkeley, CA: University of California. 264 p. Dissertation. 
148. Weise, David R.; Koo, Eunmo; Zhou, Xiangyang; Mahalingam, Shankar; Morandini, Frederic; Balbi, Jacques-Henri. 2016. Fire spread in chaparral: A comparison of laboratory data and model predictions in burning live fuels. International Journal of Wildland Fire. 25(9): 980-994. 
149. Weise, David R.; Ward, Darold E.; Paysen, Timothy E.; Koonce, Andrea L. 1991. Burning California chaparral - An exploratory study of some common shrubs and their combustion characteristics. International Journal of Wildland Fire. 1(3): 153-158. 
150. Wells, Philip V. 1968. New taxa, combinations, and chromosome numbers in Arctostaphylos (Ericaceae). Madrono. 19(6): 193-210. 
151. Wells, Philip V. 1987. The leafy-bracted, crown-sprouting manzanitas, an ancestral group in Arctostaphylos. Four Seasons. 7(4): 5-27. 
152. Westerling, A. LeRoy; Cayan, Daniel R.; Brown, Timothy J.; Riddle, Laurence G. 2004. Climate, Santa Ana winds and autumn wildfires in southern California. Eos. 85(31): 289-300. 
153. Westman, W. E. 1975. Edaphic climax pattern of the pygmy forest region of California. Ecological Monographs. 45(2): 109-135. 
154. White, Scott D.; Sawyer, John O., Jr. 1994. Dynamics of Quercus wislizenii forest and shrubland in the San Bernardino Mountains, California. Madrono. 41(4): 302-315. 
155. Wilkin, Katherine M. 2016. California forest and shrubland ecosystem changes in relation to fire, fuel hazard, and climate change. Berkeley, CA: University of California, Berkeley. 107 p. Dissertation. 
156. Wilkin, Katherine M.; Ponisio, Lauren C.; Fry, Danny L.; Tubbesing, Carmen L.; Potts, Jennifer B.; Stephens, Scott L. 2017. Decade-long plant community responses to shrubland fuel hazard reduction. Fire Ecology. 13(2): 105-136. 
157. Wilson, Bert. 2014. Leaf burn times of California native plants (& several non-native plants): California plants and fire, [Online]. Santa Margarita, CA: Las Pilitas Nursery (Producer). Available: https://www.laspilitas.com/classes/fire_burn_times.html [2019, August 22]. 
158. Wilson, R. C.; Vogl, R. J. 1965. Manzanita chaparral in the Santa Ana Mountains, California. Madrono. 18 (2): 47-62. 
159. Young, James A.; Young, Cheryl G. 1992. Seeds of woody plants in North America. [Revised and enlarged edition]. Portland, OR: Dioscorides Press. 407 p. 
160. Zedler, Paul H. 1977. Life history attributes of plants and the fire cycle: A case study in chaparral dominated by Cupressus forbesii. In: Mooney, Harold A.; Conrad, C. Eugene, technical coordinators. Proceedings of the symposium on the environmental consequences of fire and fuel management on Mediterranean ecosystems; 1977 August 1-5; Palo Alto, CA. Gen. Tech. Rep. WO-3. Washington, DC: U.S. Department of Agriculture, Forest Service: 451-458.