|An interior live oak woodland in Mariposa County, California. Photo courtesy of Charles Webber © California Academy of Sciences.|
For Quercus wislizeni var. frutescens:
scrub interior live oak
dwarf interior live oak
Quercus wislizeni A. DC. var. wislizeni, typical variety of interior live oak
Quercus wislizeni A. DC. var. frutescens Englem., scrub interior live oak
Most information on interior live oak is written at the species level. In this review, "interior live oak" refers to the species as a whole, and the varieties are referred as "the typical variety" or "scrub interior live oak".
Hybridization: Facile hybridization among red oaks makes the separation of species within that subgenus a taxonomic challenge. Among California's red oaks, interior live oak hybridizes frequently with coast live oak (Q. agrifolia) [45,46,59,61,126,198,204], Santa Cruz Island oak (Q. parvula) , California black oak (Q. kelloggii) [59,198,199], and oracle oak (Q. × moreha Kell.) . Oracle oak is a stable California black oak × interior live oak hybrid .
In California, all red oak species show some degree of introgression with other red oaks. Interior live oak populations in northern California show genetic evidence of considerable introgression with coast live oak and Shreve oak (Q. parvula var. shrevei); all 3 taxa are evergreen. Interior live oak populations show less introgression with California black oak, which is deciduous [57,58]. Backcrossing and hybrid swarms are most common between interior live oak and coast live oak , which genetic tests show are the most closely related of California's red oaks [58,61]. Dodd and others  suggest that coastal populations of interior live oak, which have high amounts of introgression overall, should be reclassified as Santa Cruz Island oak, with gene flow from interior live oak to coast live oak, then to Santa Cruz Island oak, making separation of the 3 species difficult in coastal locations. Interior live oak and Santa Cruz Island oak are sometimes treated as synonyms , but are treated as distinct species in this review.SYNONYMS:
SITE CHARACTERISTICS AND PLANT COMMUNITIES:
Site characteristics: Interior live oak mostly grows on harsh sites that other oaks cannot tolerate.
Climate and moisture regime: Interior live oak grows strictly in a mediterrean climate, which is characterized by mild, wet winters and hot, dry summers [18,22,23]. It is adapted to dry sites ; among California's red oaks, interior live oak has the highest tolerance for xeric conditions [60,179]. Mean annual precipitation across interior live oak's distribution in California ranges from 15 to 50 inches (380-1,300 mm) . Except for the deserts, the oak (Quercus spp.) woodland/grassland regions of the Sierra Nevada are driest areas in California , typically receiving <25 inches (625 mm) of precipitation annually. During the fire season, maximum summer temperatures in interior live oak foothill communities sometimes reach 105° F (41° C), with ≤5% relative humidity .
Interior live oak's evergreen leaves help protect it from desiccation, but it is not well adapted to snowy or cold sites. The branches do not hold snow loads well, and the evergreen leaves freeze easily. California black oak, which is better adapted to snow and cold, usually replaces interior live oak on upper foothills .
Interior live oak sometimes grows in riparian and other wetland areas. It may be frequent to dominant in riparian zones, especially in southern California [174,214]. In the East Bay Hills, it is a component of coast live oak communities on hillside springs .
Elevation and topography: A major vegetation survey (>17,000 plots) across California's oak communities found interior live oak had the greatest elevational range among California's 5 most frequently dominant oaks: blue oak (Q. douglasii), California black oak, canyon live oak (Q. chrysolepis), interior live oak, and valley oak (Q. lobata). Survey data suggested that interior live oak was becoming more common in montane regions compared to its 1930s distribution .
Interior live oak grows from 1,000 to 6,200 feet (300-1,900 m) elevation across its range . It tends to occur at lower elevations in northern than in southern California. Mixed-oak woodlands with interior live oak, valley oak, and/or blue oak occur from 3,000 to 4,000 feet (914-1,218 m) along the entire west slope of the Sacramento River valley . Interior live oak chaparral may occur in scattered clumps at the highest elevations (>5,500 feet (1,700 m)) of foothills in southern California . Scrub interior live oak grows at elevations from 1,000 to 6,600 feet (300-2,000 m) across its range , occurring at elevations up to 2,000 feet (600 m) in northern California  and usually from 3,500 to 6,200 feet (1,200-1,900 m) in southern California [68,99].
Landforms with interior live oak include dry valleys, canyons, and foothill slopes [68,96]. Interior live oak prefers north-facing or other relatively mesic slopes within these dry habitats [120,190]. A 1932 publication noted that on the basalt table mountains above San Joaquin Valley, interior live oak was dominant on north-facing slopes and had a scattered presence on south- and west-facing slopes. All slopes had mostly shallow soils and ephemeral streams, so they were dry for most of the year .
Soils: Interior live oak tends to occur on shallow soils in chaparral and on deeper soils in oak woodlands. Chaparral soils are nearly always dry and shallow . On sites with minimal soil development, interior live oak roots may force their way through fractured rock to reach groundwater [48,124]. The soils of California's oak woodlands are typically deep and productive [21,23]; hence, the frequent management of oak woodlands as rangelands. Interior live oak woodlands may occur on shallow to deep soils, but they generally occupy shallower soils than those of other oak series. In the San Bernardino Mountains, canyon live oak stands grade into interior live oak stands on shallow soils and ridgetops . However, interior live oak and other oak chaparral communities usually occur on relatively more productive and deeper soils than soils supporting chamise (Adenostoma fasciculatum) or manzanita (Arctostaphylos) chaparral .
Interior live oak typically grows in soil of igneous [24,128] or granitic  origin. Interior live oak communities in Tehama County have formed over volcanic breccia. Soils are 2.5 to 5 feet (0.8-1.5 m) deep and slightly acid . In the San Luis Obispo Valley, scrub interior live oak grows in siliceous sandstone . Interior live oak is rarely associated with serpentine soils . It does not grow with gray pine (Pinus sabiniana) on serpentine sites, but it is commonly associated with gray pine on nonserpentine sites [93,98]. Interior live oak does, however, grow in serpentine and other ultramafic soils in knobcone pine (P. attenuata) communities of the Klamath Mountains and the North Coast Ranges .
Interior live oak grows in soils of all textures. Interior live oak-blue oak communities in Sutter County occur on gravelly loams and shallow to moderately deep (<41 inches (100 cm)), well-drained sandy loams. One blue oak-interior live oak series had a claypan layer from 15 to 30 inches (38-76 cm) deep. Wood production of interior live oak and blue oak was greatest on sites with moderately deep soils without claypans .Plant communities:
Interior live oak communities on Table Mountain and in Coal Canyon, Butte County. Photo by Mark W. Skinner @ USDA-NRCS PLANTS Database.
Interior live oak occurs in chaparral, oak woodland, and conifer-oak woodland  communities. Typically, communities dominated by nonnative annual grasses  and/or chaparral shrubs  bound or form a mosaic with oak woodlands at low elevations, and oak woodlands meld into ponderosa pine (Pinus ponderosa) communities on upper foothills . Interior live oak scrub chaparral merges into interior live oak woodlands on some sites; a more frequent fire-return interval and/or drier soils apparently helps maintain the scrub type . Two interior live oak vegetation types were identified on the San Bernardino National Forest: chaparral and forest. Interior live oak chaparral occurred on steep (= 45°), dry slopes, and associated vegetation was mostly sprouting, sun-tolerant chaparral species including chaparral whitethorn (Ceanothus leucodermis) and chamise. Interior live oak forest occurred on more moderate ( = 20°), mesic slopes with a sparse, mixed understory of "obligate seeders" (that is, species that are killed by fire and establish afterwards from seed) and shade-tolerant sprouting shrubs such as Pacific poison-oak (Toxicodendron diversilobum). These types were not discrete on most sites; instead, the 2 types formed a blended continuum .
Gray pine and California buckeye (Aesculus californica) commonly associate with interior live oak across the ranges of all 3 species [15,18,155]. Pacific poison-oak is widespread in most woodlands with interior live oak (for example, [2,42,90,212]). As well as dominating California's annual grasslands, nonnative annual grasses comprise most of the groundlayer vegetation in California's chaparral  and oak woodlands . These annuals also dominate the groundlayer of chaparral ecosystems in Baja California . Wild oat (Avena fatua), ripgut brome (Bromus diandrus), soft chess (B. hordeaceus), and hare barley (Hordeum murinum subsp. leporinum ) are typical annual grass dominants [87,183,196]. Composition of the groundlayer prior to European settlement is unknown . Interior live oak may finger into annual grasslands on valley floors. For example, interior live oak is an occasional species in annual grasslands of El Dorado County .
Chaparral: "Chaparra" translates from Spanish to "scrub oak" in English. Scrub oak chaparral, in which scrub interior live oak is often a primary component, comprises about 15% of the chaparral landscape of California. Codominant and associated species in scrub oak chaparral are mostly shrubs such as chamise and deer brush (C. integerrimus) . The associated shrubs are often a mix of species that sprout after fire, such as chamise, and obligate seeders  such as wedgeleaf ceanothus (C. cuneatus) .
Interior live oak usually dominates the "scrub" or "live oak" chaparral vegetation types in the Inner Coast Ranges and the Sierra Nevada [23,98,106,120]. About 25% of interior live oak's total population lies within chaparral ecosystems . Sawyer and others  place a plant community in the interior live oak scrub series if >60% of the overstory is shrubby interior live oak. If cover of shrubby interior live oak is less, the series is classified as mixed chaparral . Interior live oak-dominated chaparral typically occurs on slopes; soils may be alluvial or derived from bedrock, and they are often rocky. Chamise, wedgeleaf ceanothus and other Ceanothus, and barberry-leaved scrub oak (Q. berberidifolia) often codominate with interior live oak in chaparral communities .
Northern California: In interior northern California, interior live oak is typically the dominant evergreen in scrub oak communities . Interior live oak scrub communities are most common on north-facing slopes . Chamise, manzanita, wedgeleaf ceanothus , and whitethorn ceanothus (C. cordulatus)  are common codominants or associates. Interior live oak occurs in and sometimes dominates montane chaparral in the Sierra Nevada . Van Wagtendonk  describes the montane chaparral-woodlands of Yosemite National Park as overstories of interior live oak, canyon live oak, and gray pine with whiteleaf manzanita (A. viscida), deer brush, birchleaf mountain-mahogany (Cercocarpus montanus var. glaber), and other chaparral shrubs in the midstories. A foothill mixed-chaparral type is described along the Kaweah River in Sequoia National Park. Interior live oak, California buckeye, and canyon live oak codominate the mix. Tree cover is around 40% to 60%, shrub cover from 30% to 60%, and cover of annual herbs around 50% to 75%. There has been some influx of forest conifers that is attributed to fire exclusion .
Interior live oak is a minor to important associate in scrub oak communities dominated by other oaks, usually coast live oak  or canyon live oak . Interior live oak is rare in barberry-leaved scrub oak communities of Sonoma County .
Interior live oak is a characteristic to dominant species in mixed chaparral of northern California; chamise, and sometimes barberry-leaved scrub oak, are usually codominant [98,140]. In the Outer North Coast Ranges of Santa Cruz County, interior live oak is "quite common" in the chaparral belt . In mixed chaparral near Lakeport, interior live oak and Eastwood manzanita (A. glandulosa) tend to dominate on north- and west-facing facing slopes, while chamise tends to dominate on south- and east-facing slopes .
Southern California: Interior live oak scrub communities of southern California are likely maintained by frequent fire . Coast live oak, canyon live oak , barberry-leaved scrub oak, and/or coastal sage scrub oak (Q. dumosa)  often codominate. Generally, interior live oak or coastal sage scrub oak dominate oak scrub of the Inner Southern Coast Ranges, while barberry-leaved scrub oak dominates oak scrub of the Outer Southern Coast Ranges . The interior live oak scrub vegetation type is common on xeric slopes, often sandwiched between mixed chaparral at low and conifer forests at high elevations. Shrubby interior live oaks may spread into mixed chaparral in intermittent stream draws . In the San Bernardino Mountains, interior live oak may dominate the upper reaches of barberry-leaved scrub oak and coastal sage scrub oak types . Interior live oak is the primary dominant in some oak scrub series in the western Transverse Mountains, where it codominates with canyon live oak, barberry-leaved scrub oak, birchleaf mountain-mahogany, chamise, and/or chaparral whitethorn. It is occasional in riparian coast live oak and other riparian oak woodlands .
Mexico: Interior live oak was rare in barberry-leaved scrub oak chaparral of the Sierra de San Pedro Mártir in Baja California. It was found on west-facing slopes near 5,200 feet (1,600 m) elevation .
Oak woodlands and forests: Interior live oak-dominated woodlands and occasional forests are most common in northern California, occupying west slopes of the Southern Cascade Range and the Sierra Nevada. In 1844, the explorer John Fremont made the first recorded observation of interior live oak when descending into the Sacramento Valley near the American River from upper slopes of the Sierra Nevada: "At every step the country improved in beauty; the pines were rapidly disappearing and oaks became the principal trees of the forest. Among these the prevailing tree was the evergreen live oak" . Interior live oak gains dominance with elevation in the foothills; interior live oak-gray pine woodland/annual grasslands extend from about 1,000 to 2,500 feet (300-800 m) elevation in the Sierra Nevada .
The interior live oak series is placed in the mixed broadleaved, evergreen-cold deciduous woodland formation. The series often grades in from lower-elevation interior live oak scrub. Woodlands and occasional forests dominated by tree-sized interior live oaks occur on valleys, slopes, and ridgetops; these landforms often have moderately to excessively drained, shallow soils . On foothills surrounding the Sacramento and San Joaquin valleys, interior live oak tends to dominate the drier slopes of the Sierra Nevada, while coast live oak tends to dominate the relatively wetter slopes of the Coast Ranges . Shrubs are typically chaparral types such as toyon (Heteromeles arbutifolia), wedgeleaf ceanothus, and whiteleaf manzanita. In the Sierra Nevada, interior live oak woodlands ranged from a low of 1,144 feet (249 m) for the interior live oak-gray pine/whiteleaf manzanita subseries to 2,120 feet (646 m) for the interior live oak/yerba santa (Eriodictyon californicum)/annual grass subseries . Interior live oak woodlands are rare in Pinnacles National Monument, and they are the only oak woodlands in the Monument. Sprouting shrubs, including toyon, creeping snowberry (Symphoricarpos mollis), and Pacific poison-oak are common in the type . In the San Bernardino Mountains, interior live oak may dominate upper reaches of canyon live oak woodlands .
Interior live oak is frequent to codominant in many blue oak woodlands [11,16]. Interior live oak-blue oak-gray pine communities lie just beneath the ponderosa pine belt . Blue oak-interior live oak/annual grass woodlands typically occupy the lowest foothills, with gray pine often codominating [1,2,5,98]. They average about 1,550 feet (500 m) elevation . Near Clear Lake, blue oak-interior live oak communities tend to occupy north-facing slopes, while chamise or mixed manzanita (Arctostaphylos)-chamise chaparral occupies south-facing slopes . Interior live oak is common, but rarely dominant, in blue oak communities in the low foothills of Sequoia National Park . A blue oak-interior live oak/whickerbrush (Leptosiphon ciliatus) community occurs on fine loamy soils in northern Santa Barbara County .
Many mixed-oak woodland communities contain interior live oak as an associated or codominant species. Codominant oaks may include coast live oak, blue oak, valley oak, and/or Oregon white oak (Q. garryana) in the northern portion of interior live oak's distribution and Engelmann oak (Q. engelmannii) [15,18], barberry-leaved scrub oak, and/or coastal sage scrub oak  in the south. Interior live oak is a characteristic species in some Oregon oak woodlands of the North Coast Ranges [50,98] and the Klamath Mountains . On the Hopland Research Station in Mendocino County, interior live oak codominates with coast live oak, blue oak, and California black oak . Latting  describes a northern oak woodland type that occurs inland from redwood (Sequoia sempervirens) forests north of the Bay Area. These woodlands are composed of Oregon white oak, California black oak, canyon live oak, interior live oak, and other broadleaved species. They range from 3,000 to 5,000 feet (900-2,00 m) elevation in the North Coast Ranges and the Yolla Bolly Mountains .
Interior live oak is incidental to dominant in riparian oak or other hardwood riparian communities of northern California , and it may be frequent in riparian zones of otherwise dry slopes in southern California . In riparian areas, interior live oak cover is sometimes dense enough to form a closed-canopy forest (see the photo of Coal Canyon Creek area). Interior live oak riparian communities occur below about 3,000 feet (900 m) in northern California and above about 6,000 feet (2,000 m) in southern California . In Sequoia National Park, riparian interior live oak-blue oak-California buckeye communities occur at low elevations (1,300-3,300 feet (390-1,000 m)), with denser stands than those of upland blue oak-interior live oak communities . The typical variety of interior live oak is occasional in riparian woodlands in the San Gabriel Mountains .
Conifer-oak: Interior live oak is a component of many pine-oak and other conifer-oak communities. It may finger into , and sometimes codominate in, ponderosa pine communities. In Monterey County, ponderosa pine-interior live oak-canyon live oak communities occur around 3,000 feet (900 m) elevation . Scrub interior live oak associates with knobcone pine in the North Coast Ranges [5,12]. Interior live oak is an associated species in Coulter pine (P. coulteri) communities in the Machesna Mountain Wilderness  and other locations on the Los Padres National Forest . It codominates with Coulter pine at high elevations 4,890 to 4,920 feet (1,490-1,500 m) of the Santa Lucia Range . Interior live oak associates with bishop pine (P. muricata) on Santa Cruz Island .
Mixed-evergreen and mixed-conifer zones may support interior live oaks, with interior live oaks becoming increasingly scattered with increasing elevation. The interior live oak-Pacific madrone (Arbutus menziesii)/Pacific poison-oak series occurs on mesic foothills at around 1,500 feet (450 m) in the North Coast Ranges and the Sierra Nevada . Interior live oak is a minor  to characteristic  associate in Douglas-fir-tanoak (Pseudotsuga menziesii-Lithocarpus densiflorus), Douglas-fir-Pacific madrone, and other mixed-evergreen forests. In Santa Cruz County, it was noted in a redwood-mixed evergreen-hardwood forest in Big Basin Redwoods State Park . Interior live oak was rare in redwood forests of southern Monterey County . In the Sierra Nevada, it is sometimes associated in the mixed-conifer overstory with ponderosa pine, Douglas-fir, white fir (Abies concolor), sugar pine (Pinus lambertiana), Jeffrey pine (Pinus jeffreyi), and/or red fir (A. magnifica) [67,145,166]. In mixed-evergreen forests of the Santa Lucia Range, interior live oak codominates with bristlecone fir (A. bracteata), coast live oak, and canyon live oak . On the eastern Transverse Ranges, it fingers into bigcone Douglas-fir (Pseudotsuga macrocarpa) communities from lower-elevation (~780 feet (230 m)) chamise chaparral . In the San Gabriel Mountains, interior live oak is confined to north-facing slopes and draws; bigcone Douglas-fir and canyon live oak are commonly associated species . Scrub interior live oak sprouts are often prominent in early postfire, seral bigcone Douglas-fir woodlands .See the Fire Regime Table for a list of plant communities in which interior live oak may occur and information on the fire regimes associated with those communities.
|Twig of an interior live oak near Redding, California. Photo by Julie Kierstead Nelson.|
Botanical description: This description covers characteristics that may be relevant to fire ecology and is not meant for identification. Keys for identifying California's oak species are available in these sources: [68,96]. However, identifying oaks is often difficult due to hybridization, and interior live oak hybrids are common. Tucker  pointed out that scrub oak hybrids do not "key down" well. Brophy and Parnell  provide a key to help identify interior live oak-coast live oak hybrids.
The varieties of interior live oak are distinguished by their growth form. The typical variety (Q. wislizeni var. wislizeni) grows as a tree, and scrub interior live oak (Q. wislizeni var. frutescens) grows as a shrub . The typical variety reaches from 33 to 75 feet (10-23 m) tall [96,159]. Open-grown trees have a dense, rounded crown [155,164], with branches that may extend to the ground . Trunks are one to several . Scrub interior live oak typically reaches 7 to 20 feet (2-6 m) tall  and is intricately branched . In Tehama County, interior live oak is typically 8 to 10 feet (2-3 m) tall and shrubby in form . Limited water in the substrate may be a factor driving the shrub or scrub form , although frequent fire may produce the same result. Interior live oak typically has numerous, short branches, regardless of form. In a study comparing leaf and branch architecture of 6 cooccurring sclerophyllous tree species in Mendocino County, interior live oak had more densely packed branches and leaves than Pacific madrone, canyon live oak, tanoak, giant chinquapin (Chrysolepis chrysophylla), and California bay (Umbellularia californica); this was true for both sun- and shade-grown interior live oaks .
Interior live oak wood is strong, dense, and close-grained . The bark is relatively thin [78,164] on most trees and is composed mainly of live cambium that is susceptible to fire damage. Bark of a 3-inch (7 cm) diameter interior live oak was 0.1 inch (0.3 cm) thick with a very thin layer of outer bark; bark of a 12-inch (30.5 cm) diameter tree was 0.3 inch thick with a "small amount of dead bark" on the outer surface . Bark of large trees can be up to 3.0 inches (7.5 cm) thick .
The leaves and fruits of interior live oak are relatively small. The leaves are evergreen and sclerophyllous; the margins may be spine-toothed to entire [96,164]. The leaves are elliptical and about 1 to 3 inches (2.5-8 cm) long . Male catkins are about as long as the leaves . The smaller, female flowers are born in the leaf axils in clusters of 2 to 4 . The fruits are acorns, a type of nut . They are about 0.3 to 0.5 inch (0.8-1.3 cm) wide .
Interior live oak is deep-rooted. In a review comparing maximum root depths of sclerophyllous species around the globe, interior live oak had greatest average root depths of all oaks and most other species that were compared; only Eucalyptus had greater maximum root depths . A study in Placer County found interior live oak roots extended at least 24.3 feet (7.4 m) feet through fractured rock before reaching groundwater .
Interior live oak is apparently not long-lived. Trees may live 150 to 200 years, although studies of interior live oak's longevity are few . Because interior live oaks sprout, their root systems may be several generations older than their trunks .
Interior live oak does not tolerate flooding. When the Terminus Reservoir near Visalia flooded, interior live oaks died if water covered the soil around their trunks for more than 1 week .Raunkiaer  life form:
In the Santa Lucia Mountains, time of germination initiation varied with elevation but regardless of elevation, interior live oak germination took several months to complete. Acorns began germinating in November at low elevations (76 feet (23 m)); they began germinating in December at high elevations (4,460 feet (1,360 m)). Germination was complete for acorns at low and midelevations (1,840 feet (560 m)) by February, while acorns at high elevations finished germination by March .REGENERATION PROCESSES:
Interior live oak is well adapted to regenerating after fire or cutting. The Hopland Research Field Station was nearly de-wooded from 1959 to 1965 in the belief that removing trees would provide more livestock forage and increase water yields (see Other Management Considerations for a discussion of this practice). After almost complete clearcutting except for a few large trees left for shade and a prescribed fire in 1965, a different management practice was started: Trees were allowed to regenerate. Despite the cutting and burning, oak regeneration on slopes ranging from 0° to 40° was significantly higher in 1996 compared to pretreatment levels in 1952 (P>0.05). Among tree species, interior live oak had gained greatest cover (28.4%) by 1996. This was attributed mainly to sprouting after cutting and burning .
Pollination and breeding system: Wind disperses interior live oak pollen [57,58].
Interior live oak is monoecious . Dodd and Kashani  suggest that past population fragmentation has resulted in a metapopulation structure for interior live oak. Pollen-mediated gene flow is relatively free among interior live oak populations, and introgression with other red oaks contributes to interior live oak's genetic diversity [57,58,59] (see Hybridization). For successful pollination between interior live oak and other red oaks, genetic studies show that climate compatibilities of interior live oak and the other parent are more important than distance from the pollen source .
Seed production: There are usually 5 to 7 years between large crops of interior live oak acorns (reviews by [34,159]).
Seed dispersal: Gravity and animals disperse interior live oak acorns. Scrub jays cache acorns in the ground, where unretreived acorns are likely an important source of oak regeneration .
Seed banking: Oaks have a transient seed bank . After falling off the tree, acorns remain viable only through that growing season .
Germination: Interior live oak acorns require 2 years of development on the tree to complete maturation [45,68,96].
Fresh interior live oak acorns are not dormant , so when there is enough moisture, they may germinate soon after dispersal. Fully mature, fresh acorns have germinated in the laboratory a few days after collection (review by ), and interior live oak seedlings may begin germinating in late fall in the field. Momen and others  suggest that for germination and seedling establishment, interior live oak and other evergreen oaks are adapted to use soil moisture from late-fall rains, when deciduous species are dormant. Interior live oak showed 75% mean germination after 30 to 60 days of cold stratification in the laboratory. Increased rates of interior live oak germination after cold stratification in the laboratory (review of Bonner's  laboratory studies) suggest that winter temperatures enhance its germination rates in the field.
Seedling establishment and plant growth: Little information was available as of 2011 on rates of interior live oak seedling establishment. Interior live oak showed widely different degrees of establishment on 4 sites. In Eastwood manzanita-interior live oak chaparral on Mt Tamalpais, interior live oak seedlings and saplings had an average density of 26,980 plants/ha, while interior live oak was absent from plots in Eastwood manzanita-interior live oak chaparral at Northridge. Neither site had burned for at least 56 years [109,110]. For acorns planted in interior live oak's natural elevational ranges, interior live oak showed 18% mortality at seedling emergence on the Santa Lucia Range and 2% to 5% mortality at seedling emergence in the Sierra Nevada .
Limited information suggests that interior live oak is reproducing at rates adequate to maintain its populations (, review by ). Some data suggest that interior live oak is maintaining the expected age-class distributions of more seedlings than saplings and more saplings than mature trees , but a few studies suggest rates of interior live oak regeneration may be lower than historical rates. Urban encroachment into oak woodlands poses a serious threat to interior live oak regeneration . Forest Inventory and Analysis data from 2001 to 2005 showed that across California's forestlands, interior live oak numbered about 275 million seedlings (diameter class of 1.0-2.9 inches (2.5-7.5 cm)); 125 million saplings (3.0-4.9 inches (7.6-22.9 cm)), and about 2 million relatively large trees (9.0-10.9 inches (23-27.7 cm)). Compared to California black oak, interior live oak showed higher rates of regeneration but also had higher rates of mortality . Bartolome and others [17,149] reported widespread presence of interior live oak saplings in the late 1980s, but saplings did not outnumber mature trees. Ratios of saplings:mature plants were ≤1:1 in the North Coast Ranges and Klamath-Siskiyou regions and from 1:1 to 1:2 in the Central Coast Ranges and Sierra Nevada . In manzanita chaparral in northern California, scrub interior live oak regeneration averaged ≤1.2 seedlings/m². Most were between 0 and 20 inches (8 cm) tall (Parker unpublished data cited in ). Some interior live oaks had apparently grown into the canopy since the last fire .
There is evidence that in general, many oak species in the blue oak woodland belt are failing in the pole stage , but as of this writing (2011), information of interior live oak in particular was sparse.
On 192 plots in Madera, Fresno, Tulare, and Kern counties, 75% of plots had interior live oak seedlings and 48% had saplings. Interior live oak regeneration was not significantly associated with grazing or elevation. Solar radiation, however, was positively associated with interior live oak seedling presence (P=0.1). The authors predicted that because sclerophyllous interior live oak is more drought-tolerant than deciduous blue oak, it might regenerate more successfully and dominate on drier sites than blue oak .
Interior live oak is reported as slow-growing . This is may be due to the dry habitats it typically occupies, but studies exploring interior live oak growth rates on moist vs. dry sites were not available of as 2011.
Heavy mule deer  or other browsing can reduce or eliminate interior live oak regeneration. One year following a stand-replacement wildfire on Quail Ridge Reserve near Lake Berryessa, mule deer had browsed 95% of new interior live oak sprouts. The authors suggested that mule deer's preferential selection of interior live oak and blue oak sprouts was hindering postfire regeneration of the oaks . After domestic sheep were removed from Sequoia National Park in the 1890s, there was a flush of oak (Quercus spp.) seedling establishment. The authors claim that unlike fire exclusion, which can favor shrubs over trees, density of woody species has increased since cessation of livestock grazing, but this has not resulted in a shift in species composition towards shrubs .
Vegetative regeneration: Interior live oak sprouts after top-kill by fire [87,98], cutting , or herbicide use . Field experiments in the Santa Lucia Range and the Sierra Nevada showed that damaged interior live oaks may sprout in low numbers (2%-13%) even during stages of epicotyl emergence . Large trees may produce epicormic sprouts after fire  or other injury to the bole.
A study in Mendocino County suggests that some interior live oaks may sprout after top-killing disturbances in most seasons. Sprouting responses of cut interior live oak and other oaks were compared throughout the year at the Hopland Field Station. In general, more interior live oaks sprouted after cutting compared to blue oaks; a similar number of interior live oaks and California black oaks sprouted; and fewer interior live oaks sprouted compared to barberry-leaved scrub oaks. Sprouting response of interior live oak was strongest from February through April, with 100% of cut interior live oaks sprouting during that time. Sprouting response was least in July (20%) but increased to 50% in September. Sprouts originated from both the base and the sides of interior live oak stumps. The author concluded that interior live oak was relatively insensitive to season of cutting . This study did not explore sprouting response in late fall. Biswell and Gilman  observed that interior live oaks top-killed by fire in late fall sprouted the next spring.SUCCESSIONAL STATUS:
Interior live oak may replace valley oak successionally on valley-foothill interfaces . (See the discussion of Griffin's study  in Plant response to fire for more information.) Conversely, Douglas-fir may replace interior live oak on favorable sites in mixed-evergreen communities of Mendocino County . Chaparral and oak woodlands usually remain distinct, with little conversion of one type to another .Fire is important in maintaining interior live oak chaparral and woodlands. Some consider relatively high-elevation interior live oak scrub a fire-maintained community, with ponderosa pine and other conifers replacing interior live oak without frequent fire . See Postfire successional patterns for further information on interior live oak succession.
Interior live oak's thin bark makes young trees susceptible to fire kill. Although the bark of mature trees is still relatively thin and has a high live tissue:dead outer bark ratio , mature trees may survive fire without top-kill [88,164]. Plumb and Gomez  observed that mature interior live oaks with heavily charred bark suffered no scarring and lost little bark to sloughing. They reported that surface fires rarely burned through to the wood, and repeated fires resulted in a hard, fire-cured bark surface . Haggerty , however, reports that fire scars large interior live oaks easily.
Fuel mastication in oak-knobcone pine or other communities may result in fires that are more lethal than fires in communities with unmanipulated fuels. In a California black oak-knobcone pine community in Whiskeytown National Recreation Area, sites where fuels were masticated prior to spring burning had higher flame lengths, higher fire temperatures in the litter layer, and greater mortality of overstory and pole-sized oaks—including California black, interior live, and canyon live oaks—than sites where fuels were not manipulated. Mastication was done in November, and the study sites were burned under prescription in April. Interior live oak and canyon live oak were overstory associates .
Postfire regeneration strategy :
Tree with adventitious buds and a sprouting root crown
Tall shrub, adventitious buds and a sprouting root crown
Fire adaptations and plant response to fire:
Fire adaptations: Interior live oak has adapted to fire by sprouting from perennating buds on the root crown [88,138,202]. It may sprout even in the seedling stage . Among large-fruited taxa that grow in chaparral, interior live oak is one of the most successful postfire sprouters on north-facing slopes, where it typically shades out most obligate seeders in early postfire years . Plumb and MacDonald  summarize the need of interior live oak and other California oaks for frequent fire:
"Although fire is anathema to individual oak trees, it is essential for continuation of oak stands under natural conditions, especially on commercial timber sites where inherently taller conifers are more competitive. By destroying the conifers, the oaks are free to sprout. Because of rapid sprout growth, the oaks capture the area and are perpetuated."
Although the relationship between fire frequency and Quercus regeneration is unclear, several studies show that frequent fire favors oak regeneration, reduces ladder fuels in the understory, and helps control acorn predators such as the filbert weevil and filbert worm (review by ).
Plant response to fire: Interior live oak sprouts from the root crown after top-kill by fire [24,25,28,69,83,87,98,109,181]. Postfire recovery is usually rapid . Keeley  classified interior live oak as an "obligate resprouter" after fire. Biswell and Gilman  rated it a "vigorous" sprouter after fire, showing a stronger sprouting response than associated deciduous oaks such as California black oak and blue oak. Interior live oaks often have multiple stems as a result of repeated top-kill by fire and postfire sprouting . Top-killed interior live oaks may sprout soon after winter, spring, or summer fires (see Vegetative regeneration). With summer fires, sprouts may appear as early as postfire week 3, but with late fall fires, sprouting does not usually begin until the next spring .
Large, old trees may survive fire without being top-killed  but more often, large trees are located in areas that have not burned for 50 to 100 years . Large trees may produce epicormic sprouts after surface fire  that scorches the branches.
Fire may kill interior live oak in areas with heavy fuels, particularly in chaparral or communities with a chaparral understory. In a blue oak-interior live oak-gray pine/wedgeleaf ceanothus woodland in Madera County, a prescribed 5 August fire killed 75% of interior live oaks. In postfire year 9, interior live oak comprised 15% of total woody plant species composition. A similar prescribed fire in Madera County resulted in 90% kill of interior live oak. In postfire year 7, interior live oak comprised 15% of total woody plant species composition. Chaparral whitethorn and wedgeleaf ceanothus dominated the community . Prefire composition of these plant communities was not provided.
Interior live oak may establish from acorns after fire, but postfire sprouting is far more important . One year following a stand-replacement wildfire on Quail Ridge Reserve near Lake Berryessa, density of interior live oak seedlings was not significantly different between burned and control plots. It ranged from 7 to 100 seedlings/ha. However, basal sprout regeneration was significantly greater in burned than in control plots (P<0.05) . Surveys of 91 interior live oak-dominated plots on the San Bernardino Forest found no interior live oak seedlings in interior live oak chaparral, while interior live oak forests averaged 10 interior live oak seedlings/0.1 ha. The authors suggested that longer fire-return intervals on forest plots allowed formation of the forest stand structure and establishment of interior live oak seedlings . Minnich  stated that because chaparral taxa do not rely on off-site seed dispersal onto burned sites, they are not vulnerable to fire size.
Fire scars can be ports of entry for heart-rot fungi. To date (2011), however, little research had been conducted on the relationships between fire, oaks, and heart-rot fungi .
Postfire recovery: A qualitative study on the Los Padres National Forest found interior live oak sprouted from the root crown after the Marble-Cone Wildfire of August 1977. The fire burned 178,000 acres (72,000 ha); most of this acreage was mixed chaparral. Scrub interior live oaks "were seldom completely consumed by the chaparral crown fires; they usually remained as charred trunks, perhaps five to ten feet tall, standing above the ashes". Within a month after the wildfire, they were sprouting from the root crowns and by November, the sprouts were "several feet tall". A portion of the higher-elevation, mixed-evergreen canyon live oak-tanoak-interior live oak forest also burned in the Marble-Cone Wildfire, with a mix of surface and crown fire that varied in severity from low to high. Scrub interior live oak also "sprouted readily" from the base after top-kill in this mixed-evergreen forest .
No interior live oak mortality was observed in postfire month 10 (July) after severe wildfire in September 1947 on the Tehama Deer Winter Range. All interior live oaks were top-killed, with an average sprout height of 24.9 inches (63.2 cm) in postfire month 10. Mule deer browsed the sprouts heavily the 2nd winter after the wildfire .
Prescribed fire and clearcutting may result in similar interior live oak coverage. Eight years after a moderate-severity, prescribed September fire in the Santa Ynez Mountains, interior live oak had similar densities—10 sprouts/900 m²—on burned plots and on clearcut, unburned fuelbreaks .
Although interior live oak sprouts may be dense in early postfire years, stem density usually decreases with succession. Many sprouts of chaparral species do not survive if the site burned when root crowns and roots were water-stressed and/or had low carbohydrate reserves . Heavy postfire browsing may reduce or eliminate interior live oak postfire regeneration , especially on small burns. After a 1,100-foot² (100 m²) test plot in interior live oak chaparral near Santa Cruz was burned under prescription, mule deer browsed interior live oak and California coffeberry (Rhamnus californica) sprouts so heavily that many plants of both species died, and bigberry manzanita, which was not browsed, became dominant .
Two studies, one in Sequoia National Park and the other in Madera County, show a short-term reduction in interior live oak after fire, with interior live oak showing rapid recovery in early postfire years.
In Sequoia National Park, a 26 June 1987 arson fire reduced interior live oak abundance for at least 2 postfire years. Fire conditions were "extreme", with a mean daytime air temperature of 86° F (30° C), relative humidity of 17%, and fine fuel moisture of 3.5%. Slopes ranged from 20° to 39°; mostly, dry annual grasses carried the wildfire . Fire severity was mixed, varying from low to high . Fire severity became moderate after midnight, when relative humidity rose to 50%. Fire effects and postfire responses were measured the fall after the wildfire and in postfire year 2. As measured that fall, postfire mortality of interior live oak was low: only one "very small diameter" stem had been killed. Crown scorch of interior live oaks and blue oaks combined ranged from 18% on west-facing slopes to 61% on ridgetops; bole char height ranged from 8 inches (20 cm) on west-facing slopes to 39 inches (100 cm) on east-facing slopes. Nine interior live oak seedlings were found on study sites; all were determined to have established before the fire. All 9 seedlings sprouted after the fire, but 1 seedling had died by postfire year 2 .
In postfire year 2, all large (82.6-133.4 inches (32.5-52.5 cm) diameter), crown-scorched interior live oaks had live crowns and had produced epicormic sprouts, but most smaller trees were dead . Most crown-scorched interior live oaks were <82 inches in diameter, so mortality was highest in smaller size classes . Mortality also increased with degree of crown scorch; overall, all interior live oaks with 100% crown scorch were dead, while none with <51% crown scorch had died . Some surviving crown-scorched individuals grew both epicormic and basal sprouts. Chances of interior live oak stem survival (vs. top-kill) increased with tree size (P<0.001), and 86% of large trees bore scars from previous fires. Over half of top-killed interior live oaks (n=154 individuals) had basal sprouts .
Mortality was higher for interior live oaks than for blue oaks in postfire year 2: 11% of tagged, burned interior live oaks and 6% of tagged, burned blue oaks were dead. Survival rates of postfire sprouts were higher for interior live oak than for blue oak , however, and interior live oak had more sprouts/root crown . More than half of interior live oaks that sprouted the fall after fire had surviving sprouts in postfire year 2, while only 2 top-killed blue oaks still had live sprouts .
The author concluded that the wildfire reduced interior live oak density in the short term due to aboveground mortality of small trees, but because most large trees survived, there was little change in interior live oak's basal area . See the Research Paper of this study for further details on fire effects on and postfire responses of interior live oak and blue oak.
Mechanical and prescribed fire treatments reduced interior live oak cover for about 6 years in Madera County. On the Ellis Ranch, a private cattle ranch spanning elevations from 2,500 to 3,250 feet (750-975 m), 600 acres (240 ha) of interior live oak and blue oak woodlands were thinned, then the shrub understory crushed, in July 1986. During thinning, all interior live oaks were cut for firewood but most blue oaks were retained for shade. After mechanical treatments, the site was burned under prescription in August 1986. The goals were to increase browse available for cattle and wildlife, reduce canopy cover of interior live oak, and reduce understory fuels [71,135].On 2 of 5 plots, these treatments significantly reduced interior live oak cover in postfire year 1 compared to pretreatment cover (P<0.05) .
|Interior live oak cover, density, and firewood volume after thinning, crushing, and prescribed fire in Madera County. Data are means, calculated from 5 interior live oak-blue oak or blue oak-interior live oak stands [71,135].|
|Postfire year 1
|Postfire year 2
|Postfire year 3
|Postfire year 6
|Density (stems/0.2 acre)||26.6||23.6||0||1.8||not available||not available|
|Firewood volume (cords (feet³))||1.17 (149.76)||0.72 (92.16)||0.72 (92.16)||0.17 (21.76)||0.03 (3.84)||0.03 (3.84)|
In the short term, interior live oak canopy cover and volume were reduced the most on sites where interior live oak was dominant before treatments; this was attributed more to cutting than burning. Crushing and burning successfully reduced shrub density, cover, and height, so more browse was available as forage . Interior live oak was returning to pretreatment density by postfire year 2, particularly on plots where it dominated before treatments. On all sites, wedgeleaf ceanothus and yerba santa comprised about half of the new canopy by postfire year 3 [71,135]. A follow-up prescribed fire in 3 to 4 years was recommended to once again reduce abundance of interior live oak and the shrubs . Repeat burning was not accomplished, however, so by postfire year 8, canopy cover of shrubs was similar to pretreatment levels. Interior live oak regeneration had not regained tree size, so on sites where interior live oak dominated before treatments, stand structure had shifted from an overstory of interior live oak trees to an overstory of shrubs. Blue oak was the sole overstory dominant in former blue oak-interior live oak stands .
Postfire successional patterns: Fire generally favors interior live oak  successionally. In a survey of 5 blue oak sites in Sequoia National Park, interior live oak was most frequent (15%) on a site that burned 5 years previously. The other 4 sites had not burned for about 40 years, and interior live oak frequency ranged from 5% to 10% on those sites . Minnich  noted that interior live oak and other spouting species dominated early postfire succession in Coulter pine-canyon live oak woodlands on the eastern Transverse Ranges. Vegetation from <1-year-old to 37-year-old burns was surveyed. Interior live oak was described as a dominant in early postfire succession. Interior live oak and other sprouting woody vegetation provided up to 9% cover in postfire years 0 to 9; 85% cover in postfire years 10 to 19; 75% cover in postfire years 20 to 29; and 77% cover in postfire years 30 to 37 (Minnich 1978 field data cited in ).
Surveys in southern California show that interior live oak chaparral remains stable over time. On a site that burned in a 1919 wildfire on the San Dimas Experimental Forest, Angeles National Forest, crown cover of interior live oak had not changed from that recorded in a survey conducted in postfire year 14 (1933) and in a survey conducted in postfire year 34 (1950). Interior live oak and toyon were the 2 most common species in the mixed chaparral community. Interior live oak showed minimal gains in crown cover on a similar site that had gone 55 years without fire prior to wildfires in 1933 and 1936 .
Surveys conducted by Griffin  in the Santa Lucia Mountains suggest that fire-return intervals that are longer than those that occurred historically favor interior live oak and other evergreen oaks over valley oak in high-elevation (4,575 feet (1, 525 m)) savannas. He noted that interior live oak, canyon live oak, and tanoak were replacing valley oak successionally on high-elevation sites, while coast live oak was replacing valley oak on lower-elevation sites. He suggested that this successional replacement may be occurring because in the past, frequent, low-severity surface fires favored valley oak over the evergreen oaks .FUELS AND FIRE REGIMES:
Compared to many sclerophyllous species, however, interior live oak foliage  and litter are relatively nonflammable. One comparison of the flammability of chaparral vegetation listed interior live oak as low in flammability relative to manzanita and ceanothus species, tanoak, and California black oak . Interior live oaks did not ignite during a 3 August prescribed fire in wedgeleaf ceanothus chaparral in Kern County. Interior live oaks on the site had a rounded form, with branches extending to the ground. However, the author observed that the fire "failed to affect this species" because fuels beneath interior live oak trees were scant and did not carry the fire .
Interior live oak's sclerophyllous leaves may be slow to decay. Latting  described the litter layer of interior live oak stands at the ponderosa pine-oak woodland ecotone as "slippery piles of leathery oak leaves that defy decomposition". The interior live oaks were small, with little understory beneath their crowded crowns .
Litter accumulation beneath interior live oak can vary depending, in part, on time since the last fire. Plumb and Gomez  report that the litter layer of interior live oak is typically thick. In southern California, Halsey  found barberry-leaved scrub oak-interior live oak-Muller's scrub oak (Q. cornelius-mulleri) chaparral had a "moderate" leaf litter layer (~7 inches (18 cm) thick). These communities typically occur on north-facing slopes below 3,000 feet (900 m) and on all aspects above that elevation. Overstory oaks are 4 to 12 feet (1-4 m) tall . An interior live oak-valley oak community in Tehama County had a mean litter depth of 0.5 inch (1.3 cm) in September; dried annual grasses comprised a far larger proportion of the ground layer (26.3%) than did evergreen leaves (0.6%). The canopy averaged 13.5 feet (4.1 m) tall with 25.2% closure; tree basal area averaged 7.8 m²/ha . After a fire in chaparral or oak woodlands with interior live oak, the ground layer may accumulate interior live oak debris until the decay rate equals or exceeds the rate of biomass accumulation. In burned, mixed-chaparral sites on the San Dimas Experimental Forest, biomass of interior live oak litter and woody debris increased linearly from postfire years 1 to 11 at an average rate of 0.082 ton/acre/year but then decreased without further fire .
From 1991 to 1994, the Forest Inventory and Analysis Program found that the greatest volume of live trees and coarse woody debris (CWD) of interior live oak was in the southern Sierra Nevada region (336.3 million feet³ live trees, 69.0 million feet³ CWD), and the least volume was in the North Coast Ranges (17.1 million feet³ live trees, 7.1 million feet³ CWD) (n=3,316 transects on 495 plots). Interior live oaks were considered tree-size when ≥5 inches (13 cm) DBH .
Pillsbury and Kirkley  provide equations to estimate total aboveground volume, wood volume, and saw-log volume of interior live oak and other California hardwoods.
With fire exclusion, interior live oak may become a ladder fuel in blue oak, valley oak, and other communities that historically burned less often than interior live oak-dominated communities. In oak woodland/annual grassland, dry herbaceous vegetation is the main fuel that carries fire ; however, ingrowth of understory interior live oak and ponderosa pine can increase fuel loads in and flammability of blue oak woodlands [82,154].
Fire regimes: Interior live oak is adapted to stand-replacing fires in chaparral  and frequent surface fires in oak and oak-pine woodlands ([98,180,183], review by ). Relatively frequent, recurring crown fires help maintain interior live oak chaparral . In both chaparral and oak woodlands, most wildfires historically burned down from higher-elevation conifer ecosystems [70,201]. Lightning ignitions are infrequent in chaparral and oak woodlands; historically, American Indians, miners, and ranchers were probably responsible for most fires in these communities . With a long history of fire use by American Indians and then European settlers, it is difficult to separate natural and anthropogenic fire regimes in oak woodlands . Interior live oak woodlands, and blue oak [180,183] and oak-conifer (, review by ) woodlands with a substantial interior live oak component, historically experienced mostly short return-interval surface fires, although these woodlands may also experience mixed-severity fires .
Chaparral: Chaparral ecosystems have short to moderate intervals between stand-replacement fires [113,211]. Minnich  describes a "smolder and run" behavior of chaparral fires. The fire cycle is irregular due to variations in weather and stand configurations of annual grassland-chaparral-oak woodland mosaics, but chaparral remains "remarkably stable under a wide range of fire regimes" that can vary from 20 to 100 years between fires . Fire intensity is generally high but varies with fuels and weather. Most fires occur in summer, although Santa Ana winds can drive large wildfires in autumn .
Because fire scar records are rare to lacking in chaparral ecosystems, it is difficult to determine historic fire-return intervals. They may range from 10  to as long as 60 (, reviews by [49,70]) or 100  years. Rundel  pointed out that chaparral vegetation can burn after only a few years of postfire growth. Kittredge  reported that an interior live oak chaparral site on the San Dimas Experimental Forest reburned 3 years after a previous wildfire.
Short fire-return intervals favor sprouting species such as interior live oak, while relatively long fire-return intervals favor a mix of sprouters and obligate seeder species such as wedgeleaf ceanothus  and common deerweed (Lotus scoparius) . Pioneer accounts of fire patterns in southern California chaparral suggest that before 1919, chaparral fires varied in severity across the landscape, with the low fuel loads of recent burns supporting less severe fires than the higher fuel loads of sites that had not burned in decades .
Fire exclusion may have had little effect on either fire frequency or fire size of chaparral, although experts disagree on this. Minnich [141,142] claims that in chaparral, fire size, rate of spread, and severity during extreme fire weather conditions have increased since attempts at fire exclusion. With the more even-aged structure of contemporary chaparral, Santa Ana winds tend to drive fires without the reductions in fire severity historically provided by young chaparral stands . However, Keeley and others  contend that neither fire size nor severity have increased with attempts at fire exclusion in chaparral ecosystems. Their analyses of chaparral in southern California found fire frequency increased during the last half of the 20th century, but average fire size decreased. They attributed these changes to increased anthropogenic ignitions—mostly from arson—and fire suppression. Keeley  suggests that the 30- to 40-year fire-return interval typical of California chaparral during the last half of the 20th century is more frequent than fire-return intervals of the past.
Oak woodlands: Oak woodlands, including interior live oak and blue oak-interior live oak communities, have a long history of intentional burning by American Indians and ranchers . Interior live oak woodlands and forests historically experienced mostly frequent understory surface fires . Fire-scar evidence is difficult to obtain from interior live oak and other oaks due to the prevalence of heart rot in old oaks, so fire-scarred conifers growing in oak communities are usually used to obtain fire histories . Fire-scarred ponderosa pines recorded the fire history of an interior live oak-canyon live oak-California black oak/whiteleaf manzanita (Arctostaphylos viscida)-toyon woodland in El Dorado County. From 1850 to 1952, fire-return intervals on 3 sites ranged from 2 to 18 years and averaged 7.8 years. Stand structure was likely open during that period. There was no significant difference in mean fire-return intervals among the 3 sites despite large differences in slope (5%, 30%, and 55%). Cattle ranching was the primary land use during the time studied, and the author surmised that fires were set frequently by ranchers to improve cattle forage. Before the mid-1800s, the area had been a community center for the Miwoks; unfortunately, there were no ponderosa pine trees or stumps old enough to record the fire history of that time. By the 1990s, successional changes with fire exclusion had led to a dense stand structure of 1,635 trees/ha; 75% of the basal area was oaks . Roy and Vankat  claim that excluding fire from oak woodlands can lead to a shift in species composition, with successional replacement of decadent overstory oaks by understory chaparral shrubs.
California's oak/grass woodlands historically experienced surface fires every 5 to 25 years . These frequent fires burned at low severities, which tended to kill shrub seedlings and keep the shrub layer short [88,202]. Grasses likely fueled these mostly fast-moving fires . Occasional mixed-severity fires also occurred . Because these communities form a mosaic with or lie between chaparral and low-elevation ponderosa pine woodlands, chaparral shrubs or conifers formed pockets where fire crowned, resulting in more lethal effects to vegetation, especially nonsprouting species .
Yosemite National Park's fire records from 1930 to 1983 show that lightning ignitions were relatively infrequent in the canyon live oak-interior live oak-chaparral ecosystem, but when fire occurred, it was "very intense". Fire occurrence was disproportionately low in the ecosystem (4.2% of the Park but 1.9% of fires), with a fire-return interval of about 20 to 30 years. Excepting fires <10 acres (4 ha) in size, area burned averaged 177.5 acres (71.8 ha). Because canyon live oak-interior live oak chaparral-woodlands lie outside wilderness areas of the Park, fires in this ecosystem were suppressed during the time under investigation .
Oak-conifer woodlands: Frequent fires are needed to maintain the oak component of California's oak-conifer ecosystems (for example, ), although as of 2011, information on fire regimes in interior live oak-conifer ecosystems in particular were lacking. Ponderosa pine-oak woodlands with an interior live oak component historically experienced mostly short-interval, low-severity surface fires that favored both pines and oaks (review by ). Scrub interior live oak is prominent on new burns in bigcone Douglas-fir woodlands . Little fire history was available on bigcone Douglas-fir communities as of 2011. However, bigcone Douglas-fir communities lie next to California's chaparral belt and burn often. Bigcone Douglas-fir generally survives and sprouts after surface but not after crown fires , so surface fires likely help maintain bigcone Douglas-fir communities. Walter and others  suggest that fire-return intervals in Coulter pine communities are variable. Areas going 100 or more years without fire may develop into open forests with an overstory of Coulter pine, canyon live oak, and interior live oak and an understory of chaparral whitethorn, Eastwood manzanita, and other chaparral species .
Because California's oak-conifer communities usually occur near chaparral or conifer forest ecotones and often have chaparral species in the understory, they may experience mixed or stand-replacement fires. Knobcone pine communities, in which interior live oak and other scrub oaks are often important components of the vegetation [5,12], primarily have stand-replacement fires at intervals long enough that the knobcone pine can establish and produce its serotinous cones before the next fire . Knobcone pines must be at least 10 years old to produce cones .
See the Fire Regime Table for further information on fire regimes of vegetation communities in which interior live oak 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:
Chaparral is not usually burned under prescription because of the high flammability of many chaparral species. Green  noted that chaparral can rarely be burned successfully under prescribed weather conditions because under the prescription window for weather, the shrubs are usually too moist to burn. Typically, litter and small twigs are consumed but larger stems are not, and the prescribed fire skips over large patches of brush . If prescribed burning is planned and reducing oak cover is a fire management goal, he recommended prefire preparation that top-kills and desiccates the brush, such as crushing or herbicides, with herbicides most effective on oaks and other species with thick, stout stems. See his 1977 publication  for detailed instructions on these prefire treatments, and his 1980 publication  for recommendations on preparing a prescription for burning in chaparral.
Plumb and MacDonald  consider fire an "almost inescapable occurrence" in California oak woodlands and state that trying to exclude fire from these woodlands is not practical. Periodic surface fires in oak woodlands reduce fuel loads, especially the shrub understory, and help prevent severe wildfires that can be lethal to oaks. Hence, they recommend allowing or prescribing frequent, low-severity surface fires in oak woodlands to reduce fuel loads and interference with oak growth from associated shrubs .Fires in oak woodland-chaparral communities can favor mule deer. Near Clear Lake, does averaged higher rates of ovulation on brushlands burned under prescription compared to unburned brushlands, and bucks were heavier. Blue oak-interior live oak-gray pine and chamise chaparral communities formed a mosaic in the area .
Interior live oak is an important deer food. In Lake County, mule deer browsed interior live oak year-round, with heaviest use in spring and summer . Use may also be high in winter, when deciduous species have shed their leaves, and in spring, when new shoots are available . A study on the Tehama Winter Deer Range found acorns and dry oak leaves were the primary components (65% of total) of the mule deer diet in October and November. Mule deer used interior live oak as much as expected based on its availability .
Oak/annual grassland types are California's primary livestock grazing lands [3,23,63,196]. Cattle  and domestic sheep  forage in oak woodlands on low foothills. Cattle use flat, open woodlands, while mule deer generally prefer more closed sites with rockier terrain . In Lake County, domestic sheep browsed interior live oak mostly in late spring and summer .
Many wildlife species consume interior live oak acorns, including bears [89,189], mule deer [9,24], squirrels [9,81], other rodents , acorn woodpeckers [9,116], scrub jays , and band-tailed pigeons. Acorns, including those of interior live oak, are a winter staple for band-tailed pigeons . American black bears in the Transverse Ranges consumed large volumes of acorns (canyon live oak and interior live oak, 13%-19% of total diet); behind garbage, acorns were their primary food source . Historically, the California grizzly bear, the largest race of grizzly bears , also consumed acorns . Chaparral was a preferred habitat of California grizzly bears .
Acorns can be important cattle feed; however, acorns are low in protein and become available after annual herbs have died, so cattle consuming large amounts of acorns require a protein supplement .
Habitat use: Oak woodlands, including those with interior live oak, are tremendously important wildlife habitat . A study on the Central Coast Ranges found mule deer generally preferred a mixed-oak woodland habitat over chamise chaparral, but they preferred a chamise community after a prescribed fire. Mule deer used the chamise chaparral burn as primary habitat from about postfire year 2.0 to 2.5, then resumed using the mixed-oak woodland as their primary habitat . On the Sierra Foothill Range Field Station, a 3-year study found wildlife species diversity was directly related to diversity of the mixed-oak woodland. Hutton's vireo, orange-crowned warblers, and Wilson's warblers were positively associated with interior live oak. Over 60 bird species bred and resided year-round in the oak woodland, and many others used the area as winter habitat. Several rodent and herptile species, such as brush mice and western fence lizards, were positively associated with the oak woodlands (P<0.1 for all variables). See Block and Morrison  for a list of these wildlife species. In a Kern County study, salamanders were positively associated with interior live oak-foothill pine woodlands on north-facing slopes. Except for the ground layer, vegetation cover was higher in salamander habitats than on sites without salamanders (P<0.05). Ensatina was the most commonly captured amphibian . Black-bellied, California slender, and yellow-blotched salamanders are also positively associated with interior live oaks .
On 2 sites in the Sierra Nevada and 1 in the Tehachapi Mountains, Nuttall's woodpeckers foraged heavily in interior live oak-gray pine woodlands outside the breeding season, but they used blue oak woodlands during the breeding season. Interior live oaks selected for foraging were larger than average, but acorn woodpeckers typically selected large gray pines over large interior live oaks for foraging . Surveys across California's oak woodlands found Nuttall's woodpeckers used live oaks, including interior, canyon, and coast live oaks, for foraging about 19% of the time. They used blue oak (51% use) more than the evergreen oaks but less than other deciduous oaks or gray pine .
See these sources for lists of birds using oak woodlands with interior live oak as habitat: [167,172,205].
Interior live oak woodlands are high-quality dusky-footed woodrat habitats ; in part, because they provide important food. On the San Dimas Experimental Forest in the San Gabriel Mountains, acorns of scrub interior live oaks were the primary food stored in dusky-footed woodrat nests at high elevations (>4,500 feet (1,400 m)), even though canyon live oak acorns were more plentiful and larger .
Many insects use interior live oaks as habitat. Interior live oak hosts Cynipidae gall wasps . The pan-like depressions that are created by scar tissue around branch breaks collect water in spring; these depressions are habitat to maturing insects including mosquitoes, midges, syrphid flies, and moth-flies .
Palatability and nutritional value: New spring growth and sprouts arising after fire or other top-killing events are highly palatable to mule deer . Livestock also find interior live oak palatable, and they utilize it increasingly as annual grasses dry and lose nutritional value .
Overall nutritive value of interior live oak appears low. In a laboratory experiment using captive mule deer and domestic sheep, total digestible nutrient content of interior live oak was less than that of alfalfa (Medicago sativa) or chamise. The authors concluded that interior live oak was of little to no value as a source of protein but overall, it was a fair source of total digestible nutrients . However, interior live oak provides a little protein in late fall and winter months, when deciduous browse species have shed their leaves. Bissell and Strong  found interior live oak protein content peaked in June at 8% and was least in December and February at 1%. See these sources for further details on the nutritional value of interior live oak browse: [19,20,176].
Browse of interior live oak and other evergreen oaks is generally less palatable than that of deciduous oaks due to higher concentrations of tannins and lignins in the leaves . However, domestic goats usually find interior live oak moderately to highly palatable . In the Sierra Nevada, they ate interior live oak stems "avidly" (observations by ). In mixed chaparral in southern California, domestic goats ate 5-year-old, postfire scrub interior live oak about as much as expected, preferring sprouts of birchleaf mountain-mahogany, redberry buckthorn (Rhamnus crocea), and barberry-leaved scrub oak over sprouts of interior live oak .
Cover value: Oak woodlands provide vitally important cover for wildlife. Squirrels and cavity-nesting birds often prefer cavities in oak branches or boles for nesting, while rodents, skunks, and foxes dig and den in the roots or in downed interior live oak logs .
Many wildlife species may prefer interior live oak and other evergreen oaks as cover in late fall and winter, when deciduous trees lack foliage. Feral hogs in the Sierra Nevada used interior live oak woodlands as bedding and forage sites. Their use increased in winter, when associated blue oaks had lost their leaves and provided less cover . In urban Sacramento, yellow-billed magpies selected interior live oaks as communal roosts over all other tree species during the December through May study period. Evergreen species in general were selected over deciduous species .
In a blue oak woodland on the San Joaquin Experimental Range, understory interior live oaks apparently helped protect California towhee nests from predation. On cattle-grazed sites, California towhees preferred interior live oaks for nesting (25% frequency vs. 8% frequency for all other nest-trees), and nesting success was greater in interior live oaks than in other nest-trees. For cover near the actual nest-tree, successful nests were built on sites with more understory interior live oak cover than occurred on nest-predated sites (P=0.003). Western scrub-jays were responsible for most nest predation. On ungrazed sites, California towhees preferred to nest in wedgeleaf ceanothus (18%, 4%, and 12% use for wedgeleaf ceanothus, interior live oak, and other nest-trees, respectively). Nest failure was significantly higher on ungrazed than on grazed sites (P=0.008) .VALUE FOR REHABILITATION OF DISTURBED SITES:
Acorns of interior live oak and other oaks were a staple of California Indians [8,130]. In order to produce new sprouts for basketry, Indian women used fire regularly to top-kill interior live oaks. They preferred 1-year-old sprouts for making baskets .OTHER MANAGEMENT CONSIDERATIONS:
Interior live oak is apparently resistant to sudden oak death disease. As of 2003, it was the only red oak in California in which the disease had not been detected in the field .
Possible impacts of climate change on interior live oak are uncertain. Models of McBride and Mossadegh  suggest the distributions of most California's oak species, including interior live oak, will not shift with climate change. However, paleobotanical investigations by Davis  revealed distributions of California's oak species have shifted in the past with climate change, and he predicts that the distributions of California's oaks will shift with new changes in climate. Large-scale vegetation monitoring (>17,000 plots) across California suggests that the elevational range of interior live oak is extending upslope .
Although interior live oak's value for wildlife and livestock is now appreciated, it has been disparaged in the past. In the 1950s and 1960s, some management plans called for removing oaks in general and interior live oak in particular from California's foothills in order to increase herbaceous livestock forage and water yields [21,43,64,94].These efforts greatly increased rates of soil erosion on steep slopes [43,65] and had inconsistent results regarding herbaceous forage yield production after oak removal . Studies have shown decreases , no clear trends , or increases in forage production  after interior live oak removal. In general, oak removal did little to increase water yields on foothill slopes [25,65], although some studies showed increased water yields on valley bottoms after oaks were cut .
On the San Joaquin Experimental Range, forage production was greater beneath interior live oak canopies than in the open during 2 drought years. The 1st year of the drought, herbaceous forage biomass peaked in May, at about 700 kg/ha more under interior live oak canopies than in the open. The 2nd year, forage production peaked in May at about 1,000 kg/ha more under interior live oaks than in the open. Herbaceous production early in the growing season (November-January) was similar under interior live oaks and in the open, but it was significantly greater under interior live oaks from March through May (P=0.05) . In general, late-successional annual grasses such as wild oat and ripgut brome were more common under interior live oak than in open areas. Filaree (Erodium spp.), clover (Trifolium spp.), sixweeks grass (Vulpia spp.), and other early-successional species were most common in open areas (review by ).Contrary to expectations, studies at 6 sites in northern and central California did not find a pattern of higher rates of available soil nitrogen beneath deciduous oak compared to evergreen oak species. Available soil nitrogen beneath interior live oak's canopy was similar to that beneath deciduous valley oak and higher than that beneath evergreen blue oak and deciduous California black oak (P=0.1) .
|Fire regime information on vegetation communities in which interior live oak 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
|Coastal sage scrub||Replacement||100%||50||20||150|
|Coastal sage scrub-coastal prairie||Replacement||8%||40||8||900|
|Surface or low||62%||5||1||6|
|California oak woodlands||Replacement||8%||120|
|Surface or low||91%||10|
|Surface or low||78%||13|
|California mixed evergreen||Replacement||10%||140||65||700|
|Surface or low||32%||45||7|
|Surface or low||98%||20|
|Mixed conifer (north slopes)||Replacement||5%||250|
|Surface or low||88%||15||10||40|
|Mixed conifer (south slopes)||Replacement||4%||200|
|Surface or low||80%||10|
|Surface or low||74%||30|
|Mixed evergreen-bigcone Douglas-fir (southern coastal)||Replacement||29%||250|
|Interior white fir (northeastern California)||Replacement||47%||145|
|Surface or low||21%||325|
|Red fir-white fir||Replacement||13%||200||125||500|
|Surface or low||51%||50||15||50|
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 [91,118].
1. Allen, Barbara H.; Holzman, Barbara A.; Evett, Rand R. 1991. A classification system for California's hardwood rangelands. Hilgardia. 59(2): 1-45. 
2. Allen-Diaz, Barbara H.; Holzman, Barbara A. 1991. Blue oak communities in California. Madrono. 38(2): 80-95. 
3. Allen-Diaz, Barbara; Jackson, Randall D. 2005. Herbaceous responses to livestock grazing in Californian oak woodlands: a review for habitat improvement and conservation potential. In: Kus, Barbara E.; Beyers, Jan L., tech. coords. Planning for biodiversity: Bringing research and management together: Proceedings of a symposium for the South Coast ecoregion; 29 February-2 March 2000; Pomona, CA. Gen. Tech. Rep. PSW-GTR-195. Albany, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Research Station: 127-144. 
4. Allen-Diaz, Barbara; Jackson, Randall D.; Phillips, Catherine. 2001. Spring-fed plant communities of California's East Bay Hills oak woodlands. Madrono. 48(2): 98-111. 
5. Allen-Diaz, Barbara; Standiford, Richard; Jackson, Randall D. 2007. Oak woodlands and forests. In: Barbour, Michael G.; Keeler-Wolf, Todd; Schoenherr, Allan A., eds. Terrestrial vegetation of California. Berkeley, CA: University of California Press: 313-338. 
6. Ammirati, Joseph Frank, Jr. 1967. The occurrence of annual and perennial plants on chaparral burns. San Francisco, CA: San Francisco State College. 140 p. Thesis. 
7. Anderson, M. Kat. 1999. The fire, pruning, and coppice management of temperate ecosystems for basketry material by California Indian tribes. Human Ecology. 27(1): 79-113. 
8. Anderson, M. Kat; Moratto, Michael J. 1996. Native American land-use practices and ecological impacts. In: Status of the Sierra Nevada. Sierra Nevada Ecosystem Project: Final report to Congress. Volume II: Assessments and scientific basis for management options. Wildland Resources Center Report No. 37. Davis, CA: University of California, Centers for Water and Wildland Resources: 187-206. 
9. Anderson, Melanie Vael; Pasquinelli, Renee L. 1984. Ecology and management of the northern oak woodland community, Sonoma County, California. Rohnert Park, CA: Sonoma State University. 125 p. Thesis. 
10. Arevalo, Jose Ramon; Alvarez, Pelayo; Narvaez, Nelmi; Walker, Kenny. 2009. The effetcs of fire on the regeneration of a Quercus douglasii stand in Quail Ridge Reserve, Berryessa Valley (California). Journal of Forest Research. 14(2): 81-87. 
11. Baker, Gail A.; Rundel, Philip W.; Parsons, David J. 1981. Ecological relationships of Quercus douglasii (Fagaceae) in the foothill zone of Sequoia National Park, California. Madrono. 28(1): 1-12. 
12. 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. 
13. Barrett, Reginald H. 1982. Habitat preferences of feral hogs, deer, and cattle on a Sierra foothill range. Journal of Range Management. 35(3): 342-346. 
14. Barrett, Tara; Waddell, Karen. 2008. Regeneration of California oak woodlands 2001-2005. In: Merenlender, Adina; McCreary, Douglas; Purcell, Kathryn L., tech. eds. Proceedings of the 6th symposium on oak woodlands: today's challenges, tomorrow's opportunities--Part 2; 2006 October 9-12; Rohnert Park, CA. Gen. Tech. Rep. PSW-GTR-217. Albany, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Research Station: 323-331. 
15. Bartolome, James W. 1987. California annual grassland and oak savannah. Rangelands. 9(3): 122-125. 
16. Bartolome, James W.; McClaran, Mitchel P. 1992. Composition and production of California oak savanna seasonally grazed by sheep. Journal of Range Management. 45(1): 103-107. 
17. Bartolome, James W.; Muick, Pamela C.; McClaran, Mitchel P. 1987. Natural regeneration of Californian hardwoods. 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: 26-31. 
18. Bauer, H. L. 1930. Vegetation of the Tehachapi Mountains, California. Ecology. 11(2): 263-280. 
19. Bissell, Harold D.; Strong, Helen. 1955. The crude protein variations in the browse diet of California deer. California Fish and Game. 41(2): 145-155. 
20. Bissell, Harold D.; Weir, William C. 1957. The digestibilities of interior live oak and chamise by deer and sheep. Journal of Animal Science. 16(2): 476-480. 
21. Biswell, H. H. 1954. The brush control problem in California. Journal of Range Management. 7(2): 57-62. 
22. Biswell, H. H. 1956. Ecology of California grasslands. Journal of Forestry. 9: 19-24. 
23. Biswell, H. H. 1963. Research in wildland fire ecology in California. In: Proceedings, 2nd annual Tall Timbers fire ecology conference; 1963 March 14-15; Tallahassee, FL. No. 2. Tallahassee, FL: Tall Timbers Research Station: 63-97. 
24. Biswell, H. H.; Gilman, J. H. 1961. Brush management in relation to fire and other environmental factors on the Tehama deer winter range. California Fish and Game. 47(4): 357-389. 
25. Biswell, H. H.; Schultz, A. M. 1958. Effects of vegetation removal on spring flow. California Game and Fish. 44(3): 211-230. 
26. Biswell, H. H.; Taber, R. D.; Hedrick, D. W.; Schultz, A. M. 1952. Management of chamise brushlands for game in the North Coast region of California. California Fish and Game. 38(4): 453-484. 
27. Biswell, Harold H. 1967. The Sierra Nevada: range of light. The forests - a closely woven vesture. [Lecture series given at Sierra College, Rocklin]. Davis, CA: University of California, University Extension. 19 p. On file with: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station, Fire Sciences Laboratory, Missoula, MT; FEIS files. 
28. 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. 
29. Block, William M. 1991. Foraging ecology of Nuttall's woodpecker. The Auk. 108(2): 303-317. 
30. Block, William M.; Morrison, Michael L. 1990. Wildlife diversity of the central Sierra foothills. California Agriculture. 44(2): 19-22. 
31. Block, William M.; Morrison, Michael L. 1998. Habitat relationships of amphibians and reptiles in California oak woodlands. Journal of Herpetology. 32(1): 51-60. 
32. Block, William M.; Morrison, Michael L.; Verner, Jared. 1990. Wildlife and oak-woodland interdependency. Fremontia. 18: 72-76. 
33. 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. 
34. Bonner, Franklin T. 2008. Quercus L.: oak. In: Bonner, Franklin T.; Karrfalt, Robert P., eds. Woody plant seed manual. Agric. Handbook No. 727. Washington, DC: U.S. Department of Agriculture, Forest Service: 928-938. 
35. Borchert, Mark I.; Cunha, Nancy D.; Krosse, Patricia C.; Lawrence, Marcee L. 1993. Blue oak plant communities of southern San Luis Obispo and northern Santa Barbara Counties, California. Gen. Tech. Rep. PSW-GTR-139. Albany, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Research Station. 49 p. 
36. Borchert, Mark. 1989. Postfire demography of Thermopsis macrophylla H. A. var. agnina J. T. Howell (Fabaceae), a rare perennial herb in chaparral. The American Midland Naturalist. 122(1): 120-132. 
37. Borchert, Mark; Johnson, Matthew; Schreiner, David S.; Vander Wall, Stephen B. 2003. Early postfire seed dispersal, seedling establishment and seedling mortality of Pinus coulteri (D. Don) in central coastal California, USA. Plant Ecology. 168(2): 207-220. 
38. Borchert, Mark; Schreiner, David; Knowd, Tim; Plumb, Tim. 2002. Predicting postfire survival in Coulter pine and gray pine after wildfire in central California. In: Sugihara, Neil G.; Morales, Maria; Morales, Tony, eds. Fire in California ecosystems: integrating ecology, prevention and management: Proceedings of the symposium; 1997 November 17-20; San Diego, CA. Misc. Pub. No. 1. [Berkeley, CA]: Association for Fire Ecology: 286-295. 
39. Borchert, Mark; Segotta, Daniel; Purser, Michael D. 1988. Coast redwood ecological types of southern Monterey County, California. Gen. Tech. Rep. PSW-107. Berkeley, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Forest and Range Experiment Station. 27 p. 
40. Bowcutt, Frederica S. 1999. A floristic study of Sugarloaf Ridge State Park, Sonoma County, California. Aliso. 18(1): 19-34. 
41. Boyd, Steve. 1999. Vascular flora of the Liebre Mountains, western Transverse Ranges, California. Aliso. 18(2): 93-139. 
42. Bradley, Tim; Gibson, Jennifer; Bunn, Windy. 2006. Fire severity and intensity during spring burning in natural and masticated mixed shrub woodlands. In: Andrews, Patricia L.; Butler, Bret W., comps. Fuels management--how to measure success: conference proceedings; 2006 March 28-30; Portland, OR. Proceedings RMRS-P-41. Fort Collins, CO: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station: 419-428. 
43. Brooks, Colin N.; Merenlender, Adina M. 2001. Determining the pattern of oak woodland regeneration for a cleared watershed in northwest California: a necessary first step for restoration. Restoration Ecology. 9(1): 1-12. 
44. Brooks, William H. 1967. Some quantitative aspects of the grass-oak woodland in Sequoia National Park, California. [Report to the Superintendent]. Three Rivers, CA: U.S. Department of the Interior, National Park Service, Sequoia-Kings Canyon National Park. 24 p. 
45. Brophy, William B.; Parnell, Dennis R. 1974. Hybridization between Quercus agrifolia and Q. wislizenii (Fagaceae). Madrono. 22(6): 290-302. 
46. Brophy, William. 1973. Evolution and ecology in Quercus: a study of hybridization and introgression between Quercus agrifolia Nee. and Q. wislizenii A. DC. Hayward, CA: California State University. 97 p. Thesis. 
47. Burcham, L. T. 1974. Fire and chaparral before European settlement. In: Rosenthal, Murray, ed. Symposium on living with the chaparral: Proceedings; 1973 March 30-31; Riverside, CA. San Francisco, CA: The Sierra Club: 101-120. 
48. Canadell, J.; Jackson, R. B.; Ehleringer, J. R.; Mooney, H. A.; Sala, O. E.; Schulze, E.-D. 1996. Maximum rooting depth of vegetation types at the global scale. Oecologia. 108(4): 583-595. 
49. Chang, Chi-ru. 1996. Ecosystem responses to fire and variations in fire regimes. In: Status of the Sierra Nevada. Sierra Nevada Ecosystem Project: Final report to Congress. Volume 2: Assessments and scientific basis for management options. Wildland Resources Center Report No. 37. Davis, CA: University of California, Centers for Water and Wildland Resources: 1071-1099. 
50. Clark, Harold W. 1937. Association types in the north coast ranges of California. Ecology. 18: 214-230. 
51. Conard, Susan G. 1987. First year growth of canyon live oak sprouts following thinning and clearcutting. 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: 439. 
52. Cornell, Howard V. 1985. Local and regional richness of cynipine gall wasps on California oaks. Ecology. 66(4): 1247-1260. 
53. Crosbie, Scott P.; Bell, Douglas A.; Bolen, Ginger M. 2006. Vegetative and thermal aspects of roost-site selection in urban yellow-billed magpies. The Wilson Journal of Ornithology. 118(4): 532-536. 
54. Dasmann, Raymond F. 1954. Fluctuations in a deer population in California chaparral. Transactions, North American Wildlife Conference. 21: 487-499. 
55. Davis, Owen K. 1989. Ancient analogs for greenhouse warming of central California. [Contract No. CR-814606-01-0]. In: Smith, Joel B.; Tirpak, Dennis A., eds. The potential effects of global climate change on the United States: Appendix D--Forests. EPA-230-05-89-054. Washington, D.C.: U.S. Environmental Protection Agency, Office of Policy, Planning and Evaluation: 4-1 to 4-40. 
56. DeBano, Leonard F. 1999. Chaparral shrublands in the southwestern United States. In: Ffolliott, Peter F.; Ortega-Rubio, Alfredo, eds. Ecology and management of forests, woodlands, and shrublands in the dryland regions of the United States and Mexico: perspectives for the 21st century. Co-edition No. 1. Tucson, AZ: The University of Arizona; La Paz, Mexico: Centro de Investigaciones Biologicas del Noroeste, S. C.; Flagstaff, AZ: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station: 83-94. 
57. Dodd, Richard S.; Afzal-Rafh, Zara. 2004. Selection and dispersal in a multispecies oak hybrid zone. Evolution. 58(2): 261-269. 
58. Dodd, Richard S.; Afzal-Rafii, Zara. 2004. Landscape patterns of multiple hybrid structure in California red oaks. In: Alpine diversity--adapted to the peaks: Proceedings, annual meetings of the American Bryological Society, American Fern Society, American Society of Plant Taxonomists, and Botanical Society of America; 2004 July 31-August 5; Salt Lake City, UT. St. Louis, MO: The Botanical Society of America: 112. Abstract. 
59. Dodd, Richard S.; Afzal-Rafii, Zara. 2004. Selection and dispersal in a multispecies oak hybrid zone. Evolution. 58(2): 261-269. 
60. Dodd, Richard S.; Kashani, Nasser. 2003. Molecular differentiation and diversity among the California red oaks (Fagaceae; Quercus section Lobatae). Theoretical and Applied Genetics. 107(5): 884-892. 
61. Dodd, Richard S.; Rafii, Zara A.; Bojovic, Srdjan. 1993. Chemosystematic study of hybridization in Californian live oak: acorn steroids. Biochemical Systematics and Ecology. 21(4): 467-473. 
62. Dodd, Richard S.; Rafii, Zara A.; Kashani, Nasser. 1997. Gene flow among populations of three California evergreen oaks. In: Pillsbury, Norman H.; Verner, Jared; Tietje, William D., technical coordinators. Proceedings of a symposium on oak woodlands: ecology, management, and urban interface issues; 1996 March 19-22; San Luis Obispo, CA. Gen. Tech. Rep. PSW-GTR-160. Albany, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Research Station: 127-133. 
63. Duncan, D. A.; Clawson, W. J. 1980. Livestock utilization of California's oak woodlands. In: Plumb, Timothy R., technical coordinator. Proceedings of the symposium on the ecology, management, and utilization of California oaks; 1979 June 26-28; Claremont, CA. Gen. Tech. Rep. PSW-44. Berkeley, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Forest and Range Experiment Station: 306-313. 
64. Duncan, Don A. 1968. Food of California quail on burned and unburned central California foothill rangeland. California Fish and Game. 54(2): 123-127. 
65. Dunn, Paul H.; Barro, Susan C.; Wells, Wade G., II; Poth, Mark A.; Wohlgemuth, Peter M.; Colver, Charles G. 1988. The San Dimas Experimental Forest: 50 years of research. Gen. Tech. Rep. PSW-104. Berkeley, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Forest and Range Experiment Station. 49 p. 
66. Finch, Sherman J.; McCleery, Dick. 1980. California coast live oak. In: Eyre, F. H., ed. Forest cover types of the United States and Canada. Washington, DC: Society of American Foresters: 127-128. 
67. Fites, Jo Ann. 1993. Ecological guide to mixed conifer plant associations--northern Sierra Nevada and southern Cascades: Lassen, Plumas, Tahoe, and El Dorado National Forests. R5-ECOL-TP-001. Vallejo, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Region. 120 p. 
68. Flora of North America Editorial Committee, eds. 2012. 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. 
69. 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. 
70. 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. 
71. Frost, William E. 1989. The Ellis Ranch Project: a case study in controlled burning. No. 891002. Fresno, CA: California Agricultural Technology Institute; San Joaquin Experimental Range. 11 p. 
72. Frost, William E.; Edinger, Susan B. 1991. Effects of tree canopies on soil characteristics of annual rangeland. Journal of Range Management. 44(3): 286-288. 
73. Frost, William E.; McDougald, Neil K. 1989. Tree canopy effects on herbaceous production of annual rangeland during drought. Journal of Range Management. 42(4): 281-283. 
74. Gaman, Tom; Firman, Jeffrey. 2008. Oaks 2040: the status and future of oaks in California. In: Merenlender, Adina; McCreary, Douglas; Purcell, Kathryn L., tech. eds. Proceedings of the 6th symposium on oak woodlands: today's challenges, tomorrow's opportunities--Part 2; 2006 October 9-12; Rohnert Park, CA. Gen. Tech. Rep. PSW-GTR-217. Albany, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Research Station: 603-616. 
75. Govaerts, Rafael; Frodin, David G. 1998. World checklist and bibliography of Fagales (Betulaceae, Corylaceae, Fagaceae and Ticodendraceae). Kew, UK: The Royal Botanic Gardens. 497 p. 
76. Graves, George W. 1932. Ecological relationships of Pinus sabiniana. Botanical Gazette. 94(1): 106-133. 
77. Green, Lisle R. 1977. Fuelbreaks and other fuel modifications for wildland fire control. Agric. Handb. 499. Washington, DC: U.S. Department of Agriculture, Forest Service. 79 p. 
78. Green, Lisle R. 1980. Prescribed burning in California oak management. In: Plumb, Timothy R., technical coordinator. Proceedings of the symposium on the ecology, management, and utilization of California oaks; 1979 June 24-26; Claremont, CA. Gen. Tech. Rep. PSW-44. Berkeley, CA: U.S. Department of Agriculture, Forest Service, Forest and Range Experiment Station: 136-142. 
79. 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. 
80. Greenlee, Jason. 1977. Prescribed burning program for the coastal redwoods and chaparral. 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: 397-403. 
81. Griffin, James R. 1976. Regeneration in Quercus lobata savannas, Santa Lucia Mountains, California. The American Midland Naturalist. 95(2): 422-435. 
82. Griffin, James R. 1977. Oak woodland. In: Barbour, Michael G.; Malor, Jack, eds. Terrestrial vegetation of California. New York: John Wiley and Sons: 383-415. 
83. Griffin, James R. 1978. The Marble-Cone fire ten months later. Fremontia. 6: 8-14. 
84. 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. 
85. Grinnell, Joseph. 1936. Up-hill planters. The Condor. 38: 80-82. 
86. Gutierrez, R. J.; Koenig, Walter D. 1978. Characteristics of storage trees used by acorn woodpeckers in two California woodlands. Journal of Forestry. 76(3): 162-164. 
87. Haggerty, P. K. 1994. Damage and recovery in southern Sierra Nevada foothill oak woodland after a severe ground fire. Madrono. 41(3): 185-198. 
88. Haggerty, Patricia K. 1991. Fire effects in blue oak (Quercus douglasii) woodland in the southern Sierra Nevada, California. Davis, CA: University of California. 105 p. Thesis. 
89. Halsey, Richard W. 2005. Chaparral, California's unknown wilderness. In: Halsey, Richard W. Fire, chaparral, and survival in southern California. San Diego, CA: Sunbelt Publications: 1-30. 
90. Halvorson, William L.; Clark, Ronilee A. 1989. Vegetation and floristics of Pinnacles National Monument. Tech. Rep. No. 34. Davis, CA: University of California at Davis, Institute of Ecology, Cooperative National Park Resources Study Unit. 113 p. 
91. Hann, Wendel; Havlina, Doug; Shlisky, Ayn; [and others]. 2010. Interagency fire regime condition class (FRCC) guidebook, [Online]. Version 3.0. In: FRAMES (Fire Research and Management Exchange System). National Interagency Fuels, Fire & Vegetation Technology Transfer (NIFTT) (Producer). Available: http://www.fire.org/niftt/released/FRCC_Guidebook_2010_final.pdf. 
92. Harris, Richard W.; Leiser, Andrew T.; Fissell, Robert E. 1980. Tolerance of oaks to flooding. In: Plumb, Timothy R., technical coordinator. Proceedings of the symposium on the ecology, management, and utilization of California oaks; 1979 June 26-28; Claremont, CA. Gen. Tech. Rep. PSW-44. Berkeley, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Forest and Range Experiment Station: 238-241. 
93. Harrison, Susan. 1997. How natural habitat patchiness affects the distribution of diversity in Californian serpentine chaparral. Ecology. 78(6): 1898-1906. 
94. Harvey, W. A.; Johnson, W. H.; Bell, F. L. 1959. Control of oak trees on California foothill range. Down to Earth. 15: 3-6. 
95. Hedrick, Donald W. 1951. Studies on the succession and manipulation of chamise brushlands in California. College Station, TX: Texas Agricultural and Mechanical College. 113 p. Dissertation. 
96. Hickman, James C., ed. 1993. The Jepson manual: Higher plants of California. Berkeley, CA: University of California Press. 1400 p. 
97. Holl, Stephen A.; Bleich, Vernon C.; Torres, Steven G. 2004. Population dynamics of bighorn sheep in the San Gabriel Mountains, California, 1967-2002. Wildlife Society Bulletin. 33(2): 412-426. 
98. Holland, Robert F. 1986. Preliminary descriptions of the terrestrial natural communities of California. Sacramento, CA: California Department of Fish and Game. 156 p. 
99. Horton, Jerome S. 1949. Trees and shrubs for erosion control of southern California mountains. Berkeley, CA: U.S. Department of Agriculture, Forest Service, California Forest and Range Experiment Station; California Department of Natural Resources, Division of Forestry. 72 p. 
100. 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. 
101. Hunter, J. C.; Parker, V. T. 1993. The disturbance regime of an old-growth forest in coastal California. Journal of Vegetation Science. 4(1): 19-24. 
102. Hunter, John C. 1997. Correspondence of environmental tolerance with leaf and branch attributes for six co-occurring species of broadleaf evergreen trees in northern California. Trees. 11: 169-175. 
103. Hunter, John C. 1997. Fourteen years of change in two old-growth Pseudotsuga-Lithocarpus forests in northern California. Journal of the Torrey Botanical Society. 124(4): 273-279. 
104. Hunter, John C.; Barbour, Michael G. 2001. Through-growth by Pseudotsuga menziesii: a mechanism for change in forest composition without canopy gaps. Journal of Vegetation Science. 12(4): 445-452. 
105. Jensen, Herbert A. 1939. Vegetation types and forest conditions on the Santa Cruz Mountains Unit of California. Forest Survey of California and western Nevada: Forest Survey Release No. 1. Berkeley, CA: U.S. Department of Agriculture, Forest Service, California Forest and Range Experiment Station. 55 p. 
106. Jensen, Herbet A. 1947. A system for classifying vegetation in California. California Fish and Game. 33(4): 199-266. 
107. Kartesz, John T. 1999. A synonymized checklist and atlas with biological attributes for the vascular flora of the United States, Canada, and Greenland. 1st ed. In: Kartesz, John T.; Meacham, Christopher A. Synthesis of the North American flora (Windows Version 1.0), [CD-ROM]. Chapel Hill, NC: North Carolina Botanical Garden (Producer). In cooperation with: The Nature Conservancy; U.S. Department of Agriculture, Natural Resources Conservation Service; U.S. Department of the Interior, Fish and Wildlife Service. 
108. Keeley, Jon E. 1991. Seed germination and life history syndromes in the California chaparral. The Botanical Review. 57(2): 81-116. 
109. Keeley, Jon E. 1992. Demographic structure of California chaparral in the long-term absence of fire. Vegetation Science. 3(1): 79-90. 
110. Keeley, Jon E. 1992. Recruitment of seedlings and vegetative sprouts in unburned chaparral. Ecology. 73(4): 1194-1208. 
111. Keeley, Jon E. 2006. South Coast bioregion. In: Sugihara, Neil G.; van Wagtendonk, Jan W.; Shaffer, Kevin E.; Fites-Kaufman, Joann; Thode, Andrea E., eds. Fire in California's ecosystems. Berkeley, CA: University of California Press: 350-390. 
112. Keeley, Jon E.; Fotheringham, C. J.; Morais, Marco. 1999. Reexamining fire suppression impacts on brushland fire regimes. Science. 284(5421): 1829-1831. 
113. 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. 
114. Kittredge, Joseph. 1955. Litter and forest floor of the chaparral in parts of the San Dimas Experimental Forest, California. Hilgardia. 23(13): 563-596. 
115. Klinger, Robert C.; Kutilek, Michael J.; Shellhammer, Howard S. 1989. Population responses of black-tailed deer to prescribed burning. The Journal of Wildlife Management. 53(4): 863-871. 
116. Koenig, Walter D.; McCullough, Dale R.; Vaughn, Charles E.; Knops, J. M. H.; Carmen, W. J. 1999. Synchrony and asynchrony of acorn production at two coastal California sites. Madrono. 46(1): 20-24. 
117. Kotok, E. I. 1933. Fire, a major ecological factor in the pine region of California. In: Pacific Science Congress Proceedings. 5: 4017-4022. 
118. LANDFIRE Rapid Assessment. 2005. Reference condition modeling manual (Version 2.1), [Online]. In: LANDFIRE. Cooperative Agreement 04-CA-11132543-189. Boulder, CO: The Nature Conservancy; U.S. Department of Agriculture, Forest Service; U.S. Department of the Interior (Producers). 72 p. Available: http://www.landfire.gov/downloadfile.php?file=RA_Modeling_Manual_v2_1.pdf [2007, May 24]. 
119. LANDFIRE Rapid Assessment. 2007. Rapid assessment reference condition models, [Online]. In: LANDFIRE. U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station, Fire Sciences Lab; U.S. Geological Survey; The Nature Conservancy (Producers). Available: http://www.landfire.gov/models_EW.php [2008, April 18] 
120. Latting, June, ed. 1976. Symposium proceedings--plant communities of southern California. Special Publication No. 2. Berkeley, CA: California Native Plant Society. 164 p. 
121. Laudenslayer, William F., Jr.; Fargo, Roberta J. 2002. Small mammal populations and ecology in the Kings River Sustainable Forest Ecosystems Project area. In: Verner, Jared, tech. ed. Proceedings of a symposium on the Kings River Sustainable Forest Ecosystems Project: progress and current status; 1998 January 26; Clovis, CA. Gen. Tech. Rep. PSW-GTR-183. Albany, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Research Station: 133-142. 
122. Lawrence, George E. 1966. Ecology of vertebrate animals in relation to chaparral fire in the Sierra Nevada foothills. Ecology. 47(2): 278-291. 
123. Leach, Howard R.; Hiehle, Jack L. 1956. Food habits of the Tehama deer herd. California Fish and Game. 43: 161-178. 
124. Lewis, D. C.; Burgy, R. H. 1964. The relationship between oak tree roots and groundwater in fractured rock as determined by tritium tracing. Journal of Geophysical Research. 69(12): 2579-2587. 
125. Little, Elbert L., Jr. 1976. Atlas of United States trees. Volume 3. Minor western hardwoods. Misc. Publ. 1314. Washington, DC: U.S. Department of Agriculture, Forest Service. 13 p. [+ 290 maps]. 
126. Little, Elbert L., Jr. 1979. Checklist of United States trees (native and naturalized). Agric. Handb. 541. Washington, DC: U.S. Department of Agriculture, Forest Service. 375 p. 
127. Longhurst, William M. 1956. Stump sprouting of oaks in response to seasonal cutting. Journal of Range Management. 9(4): 194-196. 
128. Lytle, Dennis J.; Finch, Sherman J. 1987. Relating cordwood production to soil series. 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: 260-267. 
129. Mackie, W. W. 1903. The value of oak leaves for forage. Bulletin No. 150. Berkeley, CA: University of California, College of Agriculture, Agricultural Experiment Station. 21 p. 
130. Martin, Glen. 1996. Keepers of the oaks. Discover. 17(8): 45-50. 
131. Matsuda, Kozue; McBride, Joe R. 1987. Germination and shoot development of seven California oaks planted at different elevations. 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: 79-85. 
132. Matsuda, Kozue; McBride, Joe R. 1989. Germination characteristics of selected California oak species. The American Midland Naturalist. 122: 66-76. 
133. McBride, Joe R.; Mossadegh, Ahmad. 1990. Will climatic change affect our oak woodlands? Fremontia. 18(3): 55-57. 
134. McDonald, Philip M. 1981. Adaptations of woody shrubs. In: Hobbs, S. D.; Helgerson, O. T., eds. Reforestation of skeletal soils: Proceedings of a workshop; 1981 November 17-19; Medford, OR. Corvallis, OR: Oregon State University, Forest Research Laboratory: 21-29. 
135. McDougald, Neil K.; Frost, William E. 1997. Assessment of a prescribed burning project: 1987-1995. In: Pillsbury, Norman H.; Verner, Jared; Tietje, William D., technical coordinators. Proceedings of a symposium on oak woodlands: ecology, management, and urban interface issues; 1996 March 19-22; San Luis Obispo, CA. Gen. Tech. Rep. PSW-GTR-160. Albany, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Research Station: 671-678. 
136. Miller, Erwin H., Jr. 1947. Growth and environmental conditions in southern California chaparral. The American Midland Naturalist. 37(2): 379-420. 
137. Miller, Howard A.; Lamb, Samuel H. 1985. Oaks of North America. Happy Camp, CA: Naturegraph Publishers. 327 p. 
138. Minnich, R.; Howard, L. 1984. Biogeography and prehistory of shrublands. In: DeVries, Johannes J., ed. Shrublands in California: literature review and research needed for management. Contribution No. 191. Davis, CA: University of California, Water Resources Center: 8-24. 
139. Minnich, Richard A. 1977. The geography of fire and big-cone Douglas-fir, Coulter pine and western conifer forests in the east Transverse Ranges, southern California. In: Mooney, Harold A.; Conrad, C. Eugene, tech. coords. 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: 443-450. 
140. Minnich, Richard A. 1980. Wildfire and the geographic relationships between canyon live oak, Coulter pine, and bigcone Douglas-fir forests. In: Plumb, Timothy R., technical coordinator. Proceedings of the symposium on the ecology, management and utilization of California oaks; 1979 June 26-28; Claremont, CA. Gen. Tech. Rep. PNW-44. Berkeley, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Forest and Range Experiment Station: 55-61. 
141. Minnich, Richard A. 1983. Fire mosaics in southern California and northern Baja California. Science. 219(4590): 1287-1294. 
142. 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. 
143. Minnich, Richard A.; Franco-Vizcaino, Ernesto. 1997. Mediterranean vegetation of northern Baja California. Fremontia. 25(3): 3-12. 
144. Mirov, N. T.; Kraebel, C. J. 1937. Collecting and propagating the seeds of California wild plants. Res. Note No. 18. Berkeley, CA: U.S. Department of Agriculture, Forest Service, California Forest and Range Experiment Station. 27 p. 
145. Molina, Domingo M.; Martin, Robert E. 1994. Prescribed burning effects on infiltration capacities in mixed-conifer forest stands at Boggs Mountain State Forest, California. In: Proceedings, 12th conference on fire and forest meteorology; 1993 October 26-28; Jekyll Island, GA. Bethesda, MD: Society of American Foresters: 663-670. 
146. Momen, B.; Menke, J. W.; Welker, J. M. 1992. Tissue water relations Quercus wislizenii seedlings: drought resistance in a California evergreen oak. Acta Oecologica. 13(1): 127-136. 
147. Morrison, Michael L.; Block, William M.; Verner, Jared. 1991. Wildlife-habitat relationships in California's oak woodlands: Where do we go from here? In: Standiford, Richard B., technical coordinator. Proceedings of the symposium on oak woodlands and hardwood rangeland management; 1990 October 31 - November 2; Davis, CA. Gen. Tech. Rep. PSW-126. Berkeley, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Research Station: 105-109. 
148. Muick, Pamela C. 1991. Effects of shade on blue oak and coast live oak regeneration in California annual grasslands. In: Standiford, Richard B., technical coordinator. Proceedings of the symposium on oak woodlands and hardwood rangeland management; 1990 October 31 - November 2; Davis, CA. Gen. Tech. Rep. PSW-126. Berkeley, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Research Station: 21-24. 
149. Muick, Pamela C.; Bartolome, James W. 1987. Factors associated with oak regeneration in California. 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: 86-91. 
150. Neff, Johnson A. 1947. Habits, food, and economic status of the band-tailed pigeon. North American Fauna 58. Washington, DC: U.S. Department of the Interior, Fish and Wildlife Service. 76 p. 
151. Nichols, R.; Adams, T.; Menke, J. 1984. Shrubland management for livestock forage. In: DeVries, Johannes J., ed. Shrublands in California: literature review and research needed for management. Contribution No. 191. Davis, CA: University of California, Water Resources Center: 104-121. 
152. Parker, V. Thomas; Billow, Christine R. 1987. Survey of soil nitrogen availability beneath evergreen and deciduous species of Quercus. 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: 98-102. 
153. 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. 
154. Parsons, David J. 1981. The historical role of fire in the foothill communities of Sequoia National Park. Madrono. 28(3): 111-120. 
155. Pavlik, Bruce M.; Muick, Pamela C.; Johnson, Sharon G.; Popper, Marjorie. 1991. Oaks of California. Los Olivos, CA: Cachuma Press. 184 p. 
156. Paysen, Timothy E.; Ansley, R. James; Brown, James K.; Gottfried, Gerald J.; Haase, Sally M.; Harrington, Michael G.; Narog, Marcia G.; Sackett, Stephen S.; Wilson, Ruth C. 2000. Fire in western shrubland, woodland, and grassland ecosystems. In: Brown, James K.; Smith, Jane Kapler, eds. Wildland fire in ecosystems: Effects of fire on flora. Gen. Tech. Rep. RMRS-GTR-42-vol. 2. Ogden, UT: U.S. Department of Agriculture, Forest Service, Rocky Mountain Research Station: 121-159. 
157. Paysen, Timothy E.; Derby, Jeanine A.; Black, Hugh, Jr.; Bleich, Vernon C.; Mincks, John W. 1980. A vegetation classification system applied to southern California. Gen. Tech. Rep. PSW-45. Berkeley, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Forest and Range Experiment Station. 33 p. 
158. Paysen, Timothy E.; Narog, Marcia G.; Tissell, Robert G.; Lardner, Melody A. 1991. Trunk and root sprouting on residual trees after thinning a Quercus chrysolepis stand. Forest Science. 37(1): 17-27. 
159. Peterson, J. S. 2002. Plant fact sheet: Interior live oak (Quercus wislizeni A. DC.), [Online]. In: PLANTS profile. In: PLANTS database. Baton Rouge, LA: U.S. Department of Agriculture, Natural Resources Conservation Service, National Plant Data Center (Producer). Available: http://plants.usda.gov/plantguide/pdf/cs_quwi2.pdf [2011, December 5]. 
160. Peterson, J. S. 2003. Plant guide: Interior live oak (Quercus wislizeni A. DC.), [Online]. In: PLANTS profile. In: PLANTS database. Baton Rouge, LA: U.S. Department of Agriculture, Natural Resources Conservation Service, National Plant Data Center (Producer). Available: http://plants.usda.gov/plantguide/pdf/cs_quwi2.pdf [2011, December 5]. 
161. 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. 
162. Pillsbury, Norman H.; Kirkley, Michael L. 1984. Equations for total, wood, and saw-log volume for thirteen California hardwoods. Research Note PNW-RN-414. Portland, OR: U.S. Department of Agriculture, Forest Service, Pacific Northwest Research Station. 52 p. 
163. Plumb, Tim R. 1980. Response of oaks to fire. In: Plumb, Timothy R., technical coordinator. Proceedings of the symposium on the ecology, management, and utilization of California oaks; 1979 June 26-28; Claremont, CA. Gen. Tech. Rep. PSW-44. Berkeley, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Forest and Range Experiment Station: 202-215. 
164. Plumb, Timothy R.; Gomez, Anthony P. 1983. Five southern California oaks: identification and postfire management. Gen. Tech. Rep. PSW-71. Berkeley, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Forest and Range Experiment Station. 56 p. 
165. Plumb, Timothy R.; McDonald, Philip M. 1981. Oak management in California. Gen. Tech. Rep. PSW-54. Berkeley, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Forest and Range Experiment Station. 11 p. 
166. Potter, Donald A. 1998. Forested communities of the upper montane in the central and southern Sierra Nevada. Gen. Tech. Rep. PSW-GTR-169. Albany, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Research Station. 319 p. 
167. Purcell, Kathryn L.; Verner, Jared. 2008. Nest-site habitat of cavity-nesting birds at the San Joaquin Experimental Range. In: Merenlender, Adina; McCreary, Douglas; Purcell, Kathryn L., tech. eds. Proceedings of the 6th symposium on oak woodlands: today's challenges, tomorrow's opportunities--Part 1; 2006 October 9-12; Rohnert Park, CA. Gen. Tech. Rep. PSW-GTR-217. Albany, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Research Station: 279-291. 
168. Purcell, Kathyrn L.; Verner, Jared. 1998. Density and reproductive success of California towhees. Conservation Biology. 12(2): 442-450. 
169. Ratliff, Raymond D.; Duncan, Don A.; Westfall, Stanley E. 1991. California oak-woodland overstory species affect herbage understory: management implications. Journal of Range Management. 44(4): 306-310. 
170. Raunkiaer, C. 1934. The life forms of plants and statistical plant geography. Oxford: Clarendon Press. 632 p. 
171. Roberts, R. Chad. 1984. The transitional nature of northwestern California riparian systems. In: Warner, Richard E.; Hendrix, Kathleen M., eds. California riparian systems: Ecology, conservation, and productive management: Proceedings of the conference; 1981 September 17-19; Davis, CA. Berkeley, CA: University of California Press: 85-91. 
172. Roberts, R. Chad. 1987. Preserving oak woodland bird species richness: suggested guidelines from geographical ecology. 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: 190-197. 
173. Rossi, Randall S. 1980. History of cultural influences on the distribution and reproduction of oaks in California. In: Plumb, Timothy R., technical coordinator. Proceedings of the symposium on the ecology, management and utilization of California oaks; 1979 June 26-28; Claremont, CA. Gen. Tech. Rep. PSW-44. Berkeley, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Forest and Range Experiment Station: 7-18. 
174. Roy, D. Graham; Vankat, John L. 1999. Reversal of human-induced vegetation changes in Sequoia National Park, California. Canadian Journal of Forest Research. 29(4): 399-412. 
175. Rundel, Philip W. 1986. Structure and function in California chaparral. Fremontia. 14(3): 3-10. 
176. Sampson, Arthur W. 1944. Plant succession on burned chaparral lands in northern California. Bull. 65. Berkeley, CA: University of California, College of Agriculture, Agricultural Experiment Station. 144 p. 
177. Sampson, Arthur W.; Burcham, L. T. 1954. Costs and returns of controlled brush burning for range improvement in northern California. Range Improvement Studies No. 1. Sacramento, CA: California Department of Natural Resources, Division of Forestry. 41 p. 
178. Sawyer, John O., Jr.; Keeler-Wolf, Todd. 1997. A manual of California vegetation, [Online]. [Sacramento, CA]: California Native Plant Society (Producer). Available: http://davisherb.ucdavis.edu/cnpsActiveServer/index.html [2012, January 25]. 
179. Sawyer, John O. 2007. Forests of northwestern California. In: Barbour, Michael G.; Keeler-Wolf, Todd; Schoenherr, Allan A., eds. Terrestrial vegetation of California. Berkeley, CA: University of California Press: 253-295. 
180. Skinner, Carl N.; Chang, Chi-ru. 1996. Fire regimes, past and present. In: Status of the Sierra Nevada. Sierra Nevada Ecosystem Project: Final report to Congress. Volume 2: Assessments and scientific basis for management options. Wildland Resources Center Report No. 37. Davis, CA: University of California, Centers for Water and Wildland Resources: 1041-1069. 
181. Skinner, Carl N.; Taylor, Alan H. 2006. Southern Cascades bioregion. In: Sugihara, Neil G.; van Wagtendonk, Jan W.; Shaffer, Kevin E.; Fites-Kaufman, Joann; Thode, Andrea E., eds. Fire in California's ecosystems. Berkeley, CA: University of California Press: 195-224. 
182. Smith, David William. 1993. Oak regeneration: the scope of the problem. In: Loftis, David L.; McGee, Charles E., eds. Oak regeneration: serious problems, practical recommendations: Symposium proceedings; 1992 September 8-10; Knoxville, TN. Gen. Tech. Rep. SE-84. Asheville, NC: U.S. Department of Agriculture, Forest Service, Southeastern Forest Experiment Station: 40-52. 
183. Standiford, Richard B. 2002. California's oak woodlands. In: McShea, William J.; Healy, William M., eds. Oak forest ecosystems: Ecology and management for wildlife. Baltimore, MD: The Johns Hopkins University Press: 280-303. 
184. Standiford, Richard B.; Howitt, Richard E. 1988. Oak stand growth on California's hardwood rangelands. California Agriculture. 42(4): 23-24. 
185. Standiford, Richard; McDougald, Neil; Frost, William; Phillips, Ralph. 1997. Factors influencing the probability of oak regeneration on southern Sierra Nevada woodlands in California. Madrono. 44(2): 170-183. 
186. Standiford, Richard; McDougald, Neil; Phillips, Ralph; Nelson, Aaron. 1991. South Sierra oak regeneration weak in sapling stage. California Agriculture. 45(2): 12-14. 
187. Stephens, Scott L. 1997. Fire history of a mixed oak-pine forest in the foothills of the Sierra Nevada, El Dorado County, California. In: Pillsbury, Norman H.; Verner, Jared; Tietje, William D., technical coordinators. Proceedings of a symposium on oak woodlands: ecology, management, and urban interface issues; 1996 March 19-22; San Luis Obispo, CA. Gen. Tech. Rep. PSW-GTR-160. Albany, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Research Station: 191-198. 
188. 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. 
189. Stubblefield, Cynthia H. 1993. Food habits of black bear in the San Gabriel Mountains of southern California. The Southwestern Naturalist. 38(3): 290-293. 
190. Taber, Richard D. 1952. Game range revegetation in California brushlands. Proceedings, 32nd Annual Conference of Western Association of State Game and Fish Commissioners. 32: 136-140. 
191. Talley, Steven Neal. 1974. The ecology of Santa Lucia fir (Abies bracteata), a narrow endemic of California. Durham, NC: Duke University. 208 p. Dissertation. 
192. The Jepson Herbarium. 2012. 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 
193. Thompson, Robert S.; Anderson, Katherine H.; Bartlein, Patrick J. 1999. Digital representations of tree species range maps from "Atlas of United States trees" by Elbert L. Little, Jr. (and other publications), [Online]. In: Atlas of relations between climatic parameters and distributions of important trees and shrubs in North America--GIS files of tree species range maps. U.S. Geological Survey Professional Paper 1650 A&B. Reston, VA: U.S. Geological Survey, Geology and Environmental Change Science Center, Earth Surface Processes (Producer). Available: http://esp.cr.usgs.gov/data/atlas/little/ [2011, June 8]. 
194. Thornburgh, Dale A. 1990. Quercus chrysolepis Liebm. canyon live oak. In: Burns, Russell M.; Honkala, Barbara H., tech. coords. Silvics of North America. Vol. 2. Hardwoods. Agric. Handbook 654. Washington, DC: U.S. Department of Agriculture, Forest Service: 618-624. 
195. Thorne, James; Bjorkman, Jacquelyn; Thrasher, Sarah; Boynton, Ryan; Kelsey, Rodd; Morgan, Brian. 2008. 1930s extent of oak species in the central Sierra Nevada. In: Merenlender, Adina; McCreary, Douglas; Purcell, Kathryn L., tech. eds. Proceedings of the 6th symposium on oak woodlands: today's challenges, tomorrow's opportunities--Part 2; 2006 October 9-12; Rohnert Park, CA. Gen. Tech. Rep. PSW-GTR-217. Albany, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Research Station: 569-587. 
196. Tietje, William D.; Barrett, Reginald H.; Kleinfelter, Eric B.; Carre, Brett T. 1991. Wildlife diversity in valley-foothill riparian habitat: North central vs. central coast California. In: Standiford, Richard B., technical coordinator. Proceedings of the symposium on oak woodlands and hardwood rangeland management; 1990 October 31 - November 2; Davis, CA. Gen. Tech. Rep. PSW-126. Berkeley, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Research Station: 120-125. 
197. Tietje, William D.; Waddell, Karen L.; Vreeland, Justin K.; Bolsinger, Charles L. 2002. Coarse woody debris in oak woodlands of California. Western Journal of Applied Forestry. 17(3): 139-146. 
198. Tucker, John M. 1980. Taxonomy of California oaks. In: Plumb, Timothy R., tech. coord. Proceedings of the symposium on the ecology, management and utilization of California oaks; 1979 June 26-28; Claremont, CA. Gen. Tech. Rep. PSW-44. Berkeley, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Forest and Range Experiment Station: 19-29. 
199. Tucker, John M. 1983. California's native oaks. Fremontia. 11(3): 3-12. 
200. U.S. Department of Agriculture, Natural Resources Conservation Service. 2012. PLANTS Database, [Online]. Available: http://plants.usda.gov/. 
201. van Wagtendonk, Jan W. 1987. The role of fire in the Yosemite Wilderness. In: Lucas, Robert C., compiler. Proceedings--national wilderness research conference: issues, state-of-knowledge, future directions; 1985 July 23-26; Fort Collins, CO. Gen. Tech. Rep. INT-220. Ogden, UT: U.S. Department of Agriculture, Forest Service, Intermountain Research Station: 135-177. 
202. van Wagtendonk, Jan W.; Fites-Kaufman, Joann. 2006. Sierra Nevada bioregion. In: Sugihara, Neil G.; van Wagtendonk, Jan W.; Shaffer, Kevin E.; Fites-Kaufman, Joann; Thode, Andrea E., eds. Fire in California's ecosystems. Berkeley, CA: University of California Press: 264-294. 
203. Vankat, John L.; Major, Jack. 1978. Vegetation changes in Sequoia National Park, California. Journal of Biogeography. 5(4): 377-402. 
204. Vasey, Michael C. 1980. Natural hybridization between two evergreen black oaks in the north central Coast Ranges of California. In: Plumb, Timothy R., technical coordinator. Proceedings of the symposium on the ecology, management and utilization of California oaks; 1979 June 26-28; Claremont, CA. Gen. Tech. Rep. PSW-44. Berkeley, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Forest and Range Experiment Station: 30-35. 
205. Verner, Jared; Purcell, Kathryn L.; Turner, Jennifer G. 1997. Bird communities in grazed and ungrazed oak-pine woodlands at the San Joaquin Experimental Range. In: Pillsbury, Norman H.; Verner, Jared; Tietje, William D., tech. coords. Proceedings of a symposium on oak woodlands: ecology, management, and urban interface issues; 1996 March 19-22; San Luis Obispo, CA. Gen. Tech. Rep. PSW-GTR-160. Albany, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Research Station: 381-390. 
206. Vogl, Richard J. 1973. Ecology of knobcone pine in the Santa Ana Mountains, California. Ecological Monographs. 43: 125-143. 
207. Wagnon, K. A. 1946. Acorns as feed for range cattle. Western Livestock Journal. 25(6): 92-94. 
208. Walter, Wartmut S.; Brennan, Teresa; Albrecht, Christian. 2005. Fire management in some California ecosystems: a cautionary note. In: Kus, Barbara E.; Beyers, Jan L., tech. coords. Planning for biodiversity: Bringing research and management together: Proceedings of a symposium for the South Coast ecoregion; 2000 February 29 - March 2; Pomona, CA. Gen. Tech. Rep. PSW-GTR-195. Albany, CA: U.S. Department of Agriculture, Forest Service, Pacific Southwest Research Station: 257-260. 
209. Weatherspoon, C. Phillip; Skinner, Carl N. 1995. An assessment of factors associated with damage to tree crowns from the 1987 wildfires in northern California. Forest Science. 41(3): 430-451. 
210. Wells, Philip V. 1962. Vegetation in relation to geological substratum and fire in the San Luis Obispo quadrangle, California. Ecological Monographs. 32(1): 79-103. 
211. 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. 
212. Wills, Robin. 2006. Central Valley bioregion. In: Sugihara, Neil G.; van Wagtendonk, Jan W.; Shaffer, Kevin E.; Fites-Kaufman, Joann; Thode, Andrea E., eds. Fire in California's ecosystems. Berkeley, CA: University of California Press: 295-320. 
213. Wilson, James L.; Ayres, Debra R.; Steinmaus, Scott; Baad, Michael. 2009. Vegetation and flora of a biodiversity hotspot: Pine Hill, El Dorado County, California, USA. Madrono. 56(4): 246-278. 
214. Wirtz, William O., II. 1977. Vertebrate post-fire succession. In: Mooney, Harold A.; Conrad, C. Eugene, technical coordinators. Symposium on the environmental consequences of fire and fuel management in Mediterranean ecosystems: Proceedings; 1977 August 1-5; Palo Alto, CA. Gen. Tech. Rep. WO-3. Washington, DC: U.S. Department of Agriculture, Forest Service: 46-57. 
215. Woodward, D. L.; Colwell, A. E.; Anderson, N. L. 1988. The aquatic insect communities of tree holes in northern California oak woodlands. Bulletin of the Society for Vector Ecology. 13(2): 221-234.