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Biomass and Burning Characteristics of Sugar Pine Cones
Fire Ecology volume 8, pages 58–70 (2012)
We investigated the physical and burning characteristics of sugar pine (Pinus lambertiana Douglas) cones and their contribution to woody surface fuel loadings. Field sampling was conducted at the Yosemite Forest Dynamics Plot (YFDP), a 25.6 ha mapped study plot in Yosemite National Park, California, USA. We developed a classification system to describe sugar pine cones of different sizes and decay conditions, and examined differences among cone classes in biomass, bulk density, flame length, burning time, consumption, and relative contribution to surface fuel loads. Sugar pine cones comprised 601 kg ha−1 of surface fuels. Mature cones comprised 54 % of cone biomass, and aborted juvenile cones accounted for 44 %. Cone biomass, diameter, and bulk density differed among cone condition classes, as did burning characteristics (one-way ANOVA, P < 0.001 in all cases). Flame lengths ranged from 5 cm to 94 cm for juvenile cones, and 71 cm to 150 cm for mature cones. Our results showed that the developmental stage at which sugar pine cones become surface fuels determines their potential contribution to surface fire behavior in Sierra Nevada mixed-conifer forests. Sugar pine cones burn with greater flame lengths and flame times than the cones of other North American fire-tolerant pine species studied to date, indicating that cones augment the surface fire regime of sugar pine forests, and likely do so to a greater degree than do cones of other pine species.
The composition, structure, and spatial heterogeneity of seasonally dry western North American mixed-conifer forests are largely determined by fire (Sugihara et al. 2006, Scholl and Taylor 2010, Larson and Churchill 2012). Land managers are increasingly seeking to restore active fire regimes in mixed-conifer forests following the period of fire exclusion in the twentieth century (e.g., Keane et al. 2006, Miller et al. 2012, van Wagtendonk et al. 2012), but reintroducing fire to landscapes in which it has been excluded requires understanding fire behavior and effects. In turn, sound fire management decisions require understanding of surface fuel properties and loads (van Wagtendonk et al. 1996, van Wagtendonk et al. 1998a, Stephens et al. 2004, Keifer et al. 2006, Hiers et al. 2009).
Surface fuel quantities and accumulation rates in the Sierra Nevada have long been recognized as high, with high forest productivity, low rates of decay in the absence of fire, and the long period of fire exclusion in the twentieth century playing a role (Keifer et al. 2006 and references therein). Components of the surface fuel complex in the Sierra Nevada have unique burning characteristics (e.g., Agee et al. 1978), and differences in the relative energy content, fuel bed properties, and physical characteristics among different fuel types has long been recognized (van Wagtendonk et al. 1996; 1998a, b). Additionally, species-specific differences in surface litter and duff fuel bed properties such as bulk density (Stephens et al. 2004) and conifer needle flammability (Fonda et al. 1998, Fonda 2001) are well known.
Pine cones are a unique woody surface fuel and relatively little is known about their contribution to surface fire behavior, although recent studies have begun to address this issue. Van Wagtendonk et al. (1998b) were apparently the first to recognize cones as a distinct fuel component with their study of heat contents of 19 Sierra Nevada conifer species. More recently, Fonda and Varner (2004) examined the burning characteristics of cones of eight North American pine species, finding that pine cones can flame for up to 15 minutes, smolder for over 80 minutes, and develop maximum flame lengths in excess of 80 cm.
Pine cones contribute to surface fire behavior and effects, possibly including mortality of large-diameter trees. The combustible nature and relatively large maximum flame lengths of cones of some tree species, particularly the larger cones that fall to the ground intact (Figure 1), suggest that they could be locally important to surface fire behavior (Mitchell et al. 2009) and may possibly spread fire to ladder fuels (Fonda and Varner 2004). Smoldering cones are thought to be vectors for duff ignition, especially when mixed with forest floor litter (Mitchell et al. 2009, Hood 2010). Pine cone combustion may be indirectly linked to fire mortality of large-diameter trees (Hood 2010), insomuch as it may act as an ignition vector for litter and duff around tree boles (Varner et al. 2009, Nesmith et al. 2010).
The cones of sugar pine (Pinus lambertiana Douglas) are among the largest of all conifers, reaching 56 cm long (Kinloch and Scheuner 1990). Sugar pine cones are a locally abundant component of the surface fuel bed in middle elevation mixed-conifer forests of the Sierra Nevada (Figure 1). Sugar pine cones were investigated by van Wagtendonk et al. (1998b) and reported to have an ash free heat content of 21.82 MJ kg−1. The burning characteristics of sugar pine cones (sensu Fonda and Varner 2004), however, are unknown. Despite their large size and local abundance, sugar pine cones remain one of the least-understood components of the surface fuel complex in Sierra Nevada mixed-conifer forests.
Sugar pine cone production takes two years and cone crops can sustain high rates of spontaneous abortion during the first year of development (Kinloch and Scheuner 1990). The sugar pine cone beetle (Conophthorus lambertianae) can cause very high (up to 93 %) rates of cone loss (Bedard 1968, Kinloch and Scheuner 1990), suggesting that aborted juvenile cones could be an episodically important component of litter fall. Additionally, Douglas-squirrel (Tamiasciurus douglasii Bachman) activity can result in high levels of cone litter fall, and squirrel activity also visibly changes the morphology and, presumably, burning characteristics of cones (Tevis 1953). Sugar pines growing in pure stands deposited cones into the surface litter at a rate of 336 kg ha−1 yr−1, but with high levels of interannual variability (290 kg ha−1 yr−1; van Wagtendonk and Moore 2010). Average deposition rate for sugar pine cones in a mixed-conifer stand was 435 kg ha−1 yr−1, accounting for up to 10 % of total annual litter fall (Stohlgren 1988). These studies only sampled recently fallen cones, however, and the relative contribution of fresh aborted first-year cones, fresh mature cones, and older partially decomposed cones (sensu Varner et al. 2009) to surface fuel loads is unknown.
The physical attributes, abundance, and burning characteristics of sugar pine cones on the forest floor constitute an important knowledge gap in the basic fire ecology of western North American mixed-conifer forests. Our field observations caused us to predict that the abundance and biomass of aborted juvenile and partially decomposed cones on the forest floor would be substantial. Further, we hypothesized that the burning characteristics of partially decomposed, fresh aborted, and fresh mature cones would differ because of the striking changes in cone morphology that occur during maturation and decomposition. We followed these predictions with three research questions:
What differences exist among mean cone biomass, diameter, and bulk density based on cone condition class (a combination of developmental stage and decomposition status)?
How abundant are sugar pine cones of different condition classes on the floor of an old-growth mixed-conifer forest?
How do burning characteristics differ among cone condition classes and relate to cone physical characteristics?
To the extent that sugar pine cones constitute a unique fuel type, with burning characteristics that vary with cone developmental stage or decomposition status, their presence could contribute to fire behavior different from that predicted with our current fuel models.
Study Site and Field Sampling
The study site was the Yosemite Forest Dynamics Plot (YFDP), a 25.6 ha study area situated at 1860 m elevation near Crane Flat in Yosemite National Park, California, USA (Lutz et al. 2012). Trees ≥1 cm dbh had been tagged, mapped, and measured using permanent monuments, providing a foundation of data for related studies. Fire has been excluded from the study site for at least 80 years, allowing deep litter and duff layers to accumulate (Lutz et al. 2012).
The YFDP is located in the white fir mixed-conifer forests of Yosemite National Park (Fites-Kaufman et al. 2007) and is typical of the white fir-sugar pine forest alliance in the Sierra Nevada (Keeler-Wolf et al. 2012). White fir (Abies concolor [Gord. & Glend.] Lindl. ex Hildebr.) is the most abundant tree species (376 trees ha−1 ≥10 cm dbh), with sugar pine second in abundance (85 trees ha−1). White fir and sugar pine have equivalent basal area (29 m2 ha−1 each) and together comprise 90 % of the basal area of the forest, with sugar pine constituting a greater proportion (69 %) of trees ≥100 cm dbh (Lutz et al. 2012). Sugar pine is a long-lived, fire-tolerant species that regenerates readily following fire, but also can establish in moderate shade. The current forest densities at the YFDP are assumed to be much higher than those prevailing prior to the period of fire exclusion (Scholl and Taylor 2010), with fire exclusion and the introduced pathogen white pine blister rust (Cronartium ribicola) assumed to be affecting current levels of regeneration, but having little effect on cone producing trees (van Mantgem et al. 2004). Along with white fir and sugar pine, canopy dominants include, in decreasing abundance, incense cedar (Calocedrus decurrens [Torr]) Florin), Douglas-fir (Pseudotsuga menziesii [Mirb.] Franco), red fir (Abies magnifica A. Murray bis) and ponderosa pine (Pinus ponderosa Lawson & C. Lawson). California black oak (Quercus kelloggii Newberry) and Pacific dogwood (Cornus nuttallii Audubon ex Torr. & A. Gray) are abundant in the lower canopy on xeric and mesic sites, respectively.
We developed a cone condition classification system based on cone size and condition attributes that could be easily estimated in the field. Categories were determined using a combination of cone developmental stage, length, and degree of decomposition (Figure 2). Cones were assigned to a condition class by simultaneously assessing size, developmental stage, and level of decomposition or animal damage. Length thresholds (Figure 2), which do not include the pedicel, were applied at a tolerance of ±20 %. The critical difference between cone classes I and II was degree of weathering and presence of resin on the scales of Class I cones, which we expected would lead to different burning characteristics (Figure 2).
To inventory cones by condition class, we placed ninety 9 m2 quadrats at randomly located points throughout the YFDP during late June 2011. Within each sample quadrat, we recorded the number of cones by condition class. We counted cones only when a portion of their volume protruded above surface litter and when >50 % of their volume lay inside the quadrat. To measure cone physical and burning characteristics, we collected five cones in each condition class from six randomly located points across the YFDP.
Laboratory Experiments and Statistical Analysis
We measured cone biomass and experimentally determined their burning characteristics at the Missoula Fire Sciences Laboratory, Missoula, Montana, USA, closely adhering to the methods of Fonda and Varner (2004). We measured maximum cone length, excluding pedicel, and diameter at the widest point of the cones. We dried the cones for at least 72 hours at 100 °C, and weighed them to obtain dry biomass. We used length and diameter measurements to estimate cone volume using the equation for the volume of a prolate spheroid,
where V is cone volume, d is cone diameter at the widest point, and L is cone length along the central axis, excluding the pedicel. We then combined the estimate of cone volume with measured cone biomass to estimate the bulk density of individual cones.
We evaluated cone flammability, fire sustainability, and consumption (sensu Fonda and Varner 2004) using a brick surface burn table ventilated by a fume hood. We weighed each cone before placing it on three kerosenesoaked cotton strings cut to the length of the cone. The strings were laid parallel on a metal tray, spaced evenly relative to cone diameter. We measured the weight of the tray, kerosenesoaked strings, and cone before ignition. We ignited the kerosene-soaked strings with a propane torch and started two timers upon cone ignition. Following Fonda and Varner (2004), we stopped the first timer when flames disappeared. The second timer measured total burning time and ran until smoke or embers were no longer visible, whichever was later. Pilot observations indicated that some combustion continued for several hours after smoke and embers ceased to be visible, but the mass loss was minimal (1 % to 2 %) so we adhered to the burning time protocol of Fonda and Varner (2004).
The mass of the tray, cone debris, and unconsumed string after burning was used to calculate total mass loss (the unconsumed string was a small portion of total mass). We subtracted flaming time from total burning time to calculate smoldering time. Flame length (flame height) was ocularly estimated using a metal ruler (with major graduations in inches) placed behind the flaming combustion zone as a reference. Maximum flame lengths were recorded for each burn.
This study used a completely randomized design. We conducted one-way ANOVA and post hoc pairwise comparisons (Tukey’s HSD) to test for differences in cone physical characteristics (oven dry mass, diameter, and bulk density) and of the burning characteristics (flaming time, smoldering time, burning time, flame length, percent mass loss, and mass loss rate) among the six cone condition classes. The interrelationships of cone bulk density and flame length, burning time, and percent mass loss were assessed with Spearman rank correlation.
We measured physical characteristics of 177 cones (Table 1). One-way ANOVA revealed differences among cone classes for the biomass, diameter, and bulk density (P < 0.001 in all cases). Post-hoc analysis showed that the two most intact mature cone condition classes (I and II) did not differ significantly from each other (Table 1). Cone physical characteristics differed significantly between mature and aborted cone condition classes, however (Table 1). Bulk density in small, aborted cones (Class V) was approximately four times higher than intact mature cones (classes I through III), reflecting the open structure of mature cones.
Abundance and Biomass
Cone density at the YFDP exceeded 10 000 cones ha−1, and biomass exceeded 600 kg ha−1 (Table 2). Aborted juvenile cones (classes V and VI) were 44 % of cone biomass on the forest floor while mature cones (classes I, II, and III) accounted for another 54 % (Table 2). Squirrel-eaten cones comprised the remaining 2 % of cone biomass on the forest floor.
Significant differences among cone classes were apparent for all burning characteristics investigated (one-way ANOVA, P < 0.001 in all cases). Recently deposited mature cones (Class I) flamed significantly longer than all other cone classes, which did not differ from each other (Table 3). Smoldering time exhibited a strikingly different pattern compared to flaming time, however, with classes I through III all smoldering for ca. 2250 s; smoldering duration was 2 to 10 times shorter for juvenile and squirrel-eaten cones (Table 3). Total burning time did not differ significantly between intact, mature cone classes (classes I through III). Total burning time was significantly longer for mature cones (classes I through III) than for aborted and squirrel-eaten cones. Juvenile aborted cones (Class VI) had the highest variance of all cone condition classes for the burning characteristics flame length, percent fuel combusted, smoldering time, and burning time, but not flaming time.
Flame length, percent mass loss, and mean rate of mass loss depended on cone condition class (one-way ANOVA, P < 0.001 in all cases). Intact mature cones (classes I and II) burned vigorously in the laboratory. Mature cone classes I and II did not differ significantly from one another in terms of burning time, flame length, or percent mass loss (Table 3, Figure 3), but aborted and squirrel-eaten cones differed significantly from the mature cones. Mean flame length for recently deposited mature cones was nearly 5 times that of aborted cones. Mass loss approached 100 % for recently dropped, mature cones, but combustion was significantly less for aborted and squirrel-eaten cones, with mass loss <34 % (Figure 3).
Spearman rank correlation analysis confirmed an inverse relationship between cone bulk density (Figure 3) and burning time (ρ =−0.58, P < 0.001), flame length (ρ = −0.62, P < 0.001), and percent mass loss (ρ = −0.68, P < 0.001).
The cone condition class model captured the variation of sugar pine cone physical characteristics. Cone length and diameter increase substantially during cone growth (Figure 2). Cone morphology also changes—small, immature cones have a closed structure of imbricate scales forming a dense shell, resulting in higher bulk density. During maturation, cone scales separate from one another as they reflex away from cone stems, resulting in higher cone volume and lower bulk density (Table 1). These changes in cone morphology alter cone surface area to volume ratio, an important determinant of fuel combustion (van Wagtendonk 2006) for which our cone bulk density measurements serve as a proxy. As a result, bulk density and length explain most of the variation in sugar pine cone structure.
The 601 kg ha−1 of sugar pine cone biomass found in this study is close to reported deposition rates of 336 kg ha−1 yr−1 in pure stands (van Wagtendonk and Moore 2010) and 435 kg ha−1 yr−1 in a mixed conifer stand (Stohlgren 1988). Our one-time measurement integrates, but does not fully capture, interannual variation in cone deposition, which varied from 200 kg ha−1 yr−1 to 800 kg ha−1 yr−1 in a mixed-conifer forest in Sequoia National Park, California, USA (Stohlgren 1988). Given reported cone deposition rates (Stohlgren 1988, van Wagtendonk and Moore 2010), our estimates of total cone biomass stocks suggest that cones decay rapidly once on the forest floor. Based on our observations in the field, physical fragmentation appears to be an important process driving the apparently rapid decomposition of cones.
Sugar pine cones comprised 1.3 % of the total forest floor fuel (duff, litter, and woody fuels <10 cm in diameter) mass in the YFDP (Lutz et al. 2012). On sites with active frequent fire regimes, sugar pine cones may comprise a larger fraction of the surface fuel load that is more in line with their relative representation in annual litterfall inputs (up to about 10 %; Stohlgren 1988): frequent fires preclude development of a deep duff layer, which should increase the proportional representation of apparently rapidly decaying pine cones in the surface fuel bed in an active fire regime (Figure 1). In addition, fire may stimulate cone production. For example, thinning alone, and in combination with prescribed fire, increased ponderosa pine cone production (Peters and Sala 2008).
Burning characteristics of sugar pine cones depended on developmental stage and degree of decomposition, supporting our initial hypothesis. Changes in cone physical structure associated with maturation—increasing cone mass and decreasing cone bulk density—precipitate accompanying changes in how cones function as surface fuels. Bulk density shares an inverse relationship with flame length, burning time, and percent mass loss (Figure 3): as cones mature they become increasingly flammable, consistent with previous work on bulk density (Burgan and Rothermel 1984). The low bulk density and high flammability of mature cones likely results from the open structure of mature cones, which increases the surface area to volume ratio, allowing for more rapid heating and drying during combustion compared to that for aborted juvenile cones.
Only flaming time differed significantly between Class I and Class II cones; other burning characteristics did not differ between these cone classes. The difference of flaming time was substantial, however, with Class I cones flaming 1.5 times longer than Class II cones. Initial weathering and loss of resin likely explain the longer flaming time of Class I compared to Class II cones. Resin has an energy content of 35.3 MJ kg−1 (Agee 1993), much higher than the 21.8 MJ kg−1 of cone tissue (van Wagtendonk et al. 1998b). The resinsealed serotinous cones of Monterey pine (Pinus radiata D. Don) and knobcone pine (Pinus attenuata Lemmon) flamed on average for 605 s and 740 s, respectively (Fonda and Varner 2004), despite their closed structure and presumably high bulk density, consistent with resin being an important determinant of pine cone flaming time.
Our laboratory measurements of cone burning characteristics implicate sugar pine cones as contributors to the surface fire regime created by litterfall in Sierra Nevada mixed-conifer forests (sensu Fonda and Varner 2004). Sugar pine cones burn with greater flame lengths and longer flaming times than cones of ponderosa pine and Jeffrey pine (Pinus jeffreyi Balf.), two other pine species that commonly co-occur with sugar pine. Maximum flame length and flame duration for mature sugar pine cones exceeded previously reported values for ponderosa pine and Jeffrey pine by ca. 58 cm and 120 s (Fonda and Varner 2004). The relatively greater potential contribution of sugar pine cones to surface fire behavior compared to cones of ponderosa pine and Jeffrey pine becomes more apparent when burning characteristics of cones are considered alongside those of conspecific foliage. Maximum flame lengths of ponderosa pine and Jeffrey pine needles were similar to maximum flame lengths of conspecific cones (Fonda et al. 1998). Maximum flame lengths of sugar pine cones, however, were twice that of sugar pine needles, in addition to cones having longer flaming time and smoldering time compared to needles (Fonda et al. 1998). Thus, it appears that sugar pine cones can be relatively greater contributors to surface fire behavior than cones of ponderosa pine or Jeffrey pine. By enhancing the flammability of the surface fuels, sugar pine cones may play an important role in the fuel dynamics of in mixed-conifer forests that lack a significant ponderosa pine or Jeffrey pine component, such as the YFDP.
Mature sugar pine cones, with flame lengths >1 m and flame duration of 3 min to 6 min, clearly have the potential to contribute to surface fire behavior and spread (Fonda and Varner 2004). Under some circumstances, flaming mature cones might also ignite shrubs and tree saplings. Burning cones also contribute to fire spread when they roll downhill beyond the fire perimeter, part of the reason for the practice of cup-trenching fire lines on steep terrain. Cones that smolder for long periods, such as the approximately 35 min smoldering times observed here for classes I through III, become potential ignition sources in the litter and duff layers with negative consequences for large tree survival (Hood 2010). Our laboratory measurements did not examine differences in burning characteristics due to different moisture contents or due to admixtures of cones and needles (sensu Taylor and Fonda 1990, Fonda and Varner 2004). A combination of laboratory and field experiments would provide insights into the role of sugar pine cones as a flame and heat vector for surface and ladder fuel ignition, or as a vector for duff ignition.
Although sugar pine cones do not necessarily drive surface fire dynamics throughout the forest, at small spatial scales they are locally abundant (Figure 1) and likely influence fire behavior and effects at such scales. Microtopography, down coarse woody debris, and the spatial arrangement of large diameter coneproducing trees cause the abundance of sugar pine cones on the forest floor to vary spatially. Accumulations of sugar pine cones that may increase the severity of surface fire locally could, for example, contribute to the small-scale (15 m to 20 m) spatial heterogeneity observed in these mixed-conifer forests (e.g., Larson and Churchill 2012, Lutz et al. 2012) through increased mortality of smaller trees. Fonda and Varner (2004) advanced a similar hypothesis, noting that cones of ponderosa pine and Jeffrey pine are frequently aggregated around tree bases and therefore may contribute to maintenance of a low-competition environment in the immediate tree neighborhood when they burn. Further study is warranted, given the vigorous burning characteristics of individual sugar pine cones in the laboratory, of spatial patterns of cone accumulation on the forest floor and the burning characteristics of aggregations of cones.
We discovered that sugar pine cones burn with greater flame lengths and flaming times than the cones of other North American resister pines (sensu Agee 1993) studied to date. Sugar pine cone flaming times were only exceeded by the resin-coated serotinous cones of knobcone pine and Monterey pine (Fonda and Varner 2004). Sugar pine cones burned with greater flame length, flaming time, smoldering time, and mass loss than sugar pine foliage (Fonda et al. 1998), indicating that cones augment surface fire behavior of sugar pine forests, and likely do so to a greater degree than do cones of other resister pine species (Fonda 2001, Fonda and Varner 2004). Finally, we found that flammability of sugar pine cones varied dramatically and was dependent on degree of cone maturation and post-deposition decomposition. Our results indicate that the developmental stage at which cones become surface fuels and the time since deposition exert strong control over the contribution of sugar pine cones to surface fire behavior.
Agee, J.K. 1993. Fire ecology of Pacific Northwest forests. Island Press, Washington, D.C., USA.
Agee, J.K., R.H. Wakimoto, and H.H. Biswell. 1978. Fire and fuel dynamics of Sierra Nevada conifers. Forest Ecology and Management 1: 255–265. doi: 10.1016/0378-1127(76)90030-X
Bedard, W. 1968. The sugar pine cone beetle. Forest pest leaflet 112. US Department of Agriculture, Forest Service, Washington, D.C., USA.
Burgan, R.E., and R.C. Rothermel. 1984. BEHAVE: Fire prediction and modeling system— FUEL subsystem. General Technical Report INT-167. US Department of Agriculture, Forest Service, Intermountain Forest and Range Research Station, Ogden, Utah, USA.
Fites-Kaufman, J., P. Rundel, N. Stephenson, and D. A. Weixelman. 2007. Montane and subalpine vegetation of the Sierra Nevada and Cascade ranges. Pages 456–501 in: M.G. Barbour, T. Keeler-Wolf, and A.A. Schoenherr, editors. Terrestrial vegetation of California. University of California Press, Berkeley, USA.
Fonda, R.W. 2001. Burning characteristics of needles from eight pine species. Forest Science 47: 390–396.
Fonda, R.W., L.A. Belanger, and L.L. Burley. 1998. Burning characteristics of western conifer needles. Northwest Science 72: 1–9.
Fonda, R.W., and J.M. Varner. 2004. Burning characteristics of cones from eight pine species. Northwest Science 78: 322–333.
Hiers, J.K., J.J. O’Brien, R.J. Mitchell, J.M. Grego, and E.L. Loudermilk. 2009. The wildland fuel cell concept: an approach to characterize fine-scale variation in fuels and fire in frequently burned longleaf pine forests. International Journal of Wildland Fire 18: 315–325. doi: 10.1071/WF08084
Hood, S.M. 2010. Mitigating old tree mortality in long-unburned, fire dependent forests: a synthesis. General Technical Report RMRS-GTR-238. US Department of Agriculture, Forest Service, Rocky Mountain Research Station, Fort Collins, Colorado, USA.
Keane, R.E., S. Arno, and L.J. Dickinson. 2006. The complexity of managing fire-dependent ecosystems in wilderness: relict ponderosa pine in the Bob Marshall Wilderness. Ecological Restoration 24: 71–78. doi: 10.3368/er.24.2.71
Keeler-Wolf, T., P.E. Moore, E.T. Reyes, J.M. Menke, D.N. Johnson, and D.L. Karavidas. 2012. Yosemite National Park vegetation classification and mapping project report. Natural Resource Technical Report NPS/YOSE/NRTR—2012/598. National Park Service, Fort Collins, Colorado, USA.
Keifer, M.B., J.W. van Wagtendonk, and M. Buhler. 2006. Long-term surface fuel accumulation in burned and unburned mixed-conifer forests of the central and southern Sierra Nevada, CA USA. Fire Ecology 2(1): 53–72. doi: 10.4996/fireecology.0201053
Kinloch, B.B., and W.H. Scheuner. 1990. Pinus lambertiana Dougl., sugar pine. Pages 370–379 in: R.M. Burns and B.H. Honkala, technical coordinators. Silvics of North America: 1. Conifers. Agriculture Handbook 654. US Department of Agriculture, Forest Service, Washington, D.C., USA.
Larson, A.J., and D. Churchill. 2012. Tree spatial patterns in fire-frequent forests of western North America, including mechanisms of pattern formation and implications for designing fuel reduction and forest restoration treatments. Forest Ecology and Management 267: 74–92. doi: 10.1016/j.foreco.2011.11.038
Lutz, J.A., A.J. Larson, M.E. Swanson, and J.A. Freund. 2012. Ecological importance of large-diameter trees in a temperate mixed-conifer forest. PLoS ONE 7(5): e36131. doi: 10.1371/journal.pone.0036131
Miller, J.D., B.M. Collins, J.A. Lutz, S.L. Stephens, J.W. van Wagtendonk, and D.A. Yasuda. 2012. Differences in wildfires among ecoregions and land management agencies in the Sierra Nevada region, California, USA. Ecosphere 3(9): 80. doi: 10.1890/ES12-00158.1
Mitchell, R.J., J.K. Hiers, J. O’Brien, and G. Starr. 2009. Ecological forestry in the Southeast: understanding the ecology of fuels. Journal of Forestry 107: 391–397.
Nesmith, J.C.B, K.L. O’Hara, P.J. van Mantgem, and P. de Valpine. 2010. The effects of raking on sugar pine mortality following prescribed fire in Sequoia and Kings Canyon National Parks, California, USA. Fire Ecology 6(3): 97–116. doi: 10.4996/fireecology.0603097
Peters, G., and A. Sala. 2008. Reproductive output of ponderosa pine in response to thinning and prescribed burning in western Montana. Canadian Journal of Forest Research 38: 844–850. doi: 10.1139/X07-203
Scholl, A.E., and A.H. Taylor. 2010. Fire regimes, forest change, and self-organization in an old-growth mixed-conifer forest, Yosemite National Park, USA. Ecological Applications 20 (2): 362–380. doi: 10.1890/08-2324.1
Stephens, S.L., M.A. Finney, and H. Schantz. 2004. Bulk density and fuel loads of ponderosa pine and white fir forest floors: impacts of leaf morphology. Northwest Science 78: 93–100.
Stohlgren, T.J. 1988. Litter dynamics of two Sierran mixed-conifer forests. I: litterfall and decomposition rates. Canadian Journal of Forest Research 18: 1127–1135. doi: 10.1139/x88-174
Sugihara, N.G., J.W. van Wagtendonk, K.E. Shaffer, J. Fites-Kaufman, and A.E. Thode. 2006. Fire in California’s ecosystems. University of California Press, Berkeley, USA. doi: 10.1525/california/9780520246058.001.0001
Taylor, K.L., and R.W. Fonda. 1990. Woody fuel structure and fire in subalpine fir forests, Olympic National Park, Washington. Canadian Journal of Forest Research 20: 193–199. doi: 10.1139/x90-027
Tevis, L. 1953. Effect of vertebrate animals on seed crop of sugar pine. The Journal of Wildlife Management 17: 128–131. doi: 10.2307/3796707
van Mantgem, P.J., N.L. Stephenson, M. Keifer, and J. Keeley. 2004. Effects of an introduced pathogen and fire exclusion on the demography of sugar pine. Ecological Applications 14: 1590–1602. doi: 10.1890/03-5109
van Wagtendonk, J.W. 2006. Fire as a physical process. Pages 38–57 in: N.G. Sugihara, J.W. van Wagtendonk, K.E. Shaffer, J. Fites-Kaufman, and A.E. Thode, editors. Fire in California’s ecosystems. University of California Press, Berkeley, USA.
van Wagtendonk, J.W., J.M. Benedict, and W.M. Sydoriak. 1996. Physical properties of woody fuel particles of Sierra Nevada conifers. International Journal of Wildland Fire 6: 117–123. doi: 10.1071/WF9960117
van Wagtendonk, J.W., J.M Benedict, and W.M. Sydoriak. 1998a. Fuel bed characteristics of Sierra Nevada conifers. Western Journal of Applied Forestry 13: 73–84.
van Wagtendonk, J.W., and P.E. Moore. 2010. Fuel deposition rates of montane and subalpine conifers in the central Sierra Nevada, California, USA. Forest Ecology and Management 259: 2122–2132. doi: 10.1016/j.foreco.2010.02.024
van Wagtendonk, J.W., W.M. Sydoriak, and J.M. Benedict. 1998b. Heat content variation of Sierra Nevada conifers. International Journal of Wildland Fire 8:147–158. doi: 10.1071/WF9980147
van Wagtendonk, J.W., K.A. van Wagtendonk, and A.E. Thode. 2012. Factors associated with the severity of intersecting fires in Yosemite National Park, California, USA. Fire Ecology 8(1): 11–31. doi: 10.4996/fireecology.0801011
Varner, J.M., F.E. Putz, J.J. O’Brien, J.K. Hiers, R.J. Mitchell, and D.R. Gordon. 2009. Post-fire tree stress and growth following smoldering duff fires. Forest Ecology and Management 258: 2467–2474. doi: 10.1016/j.foreco.2009.08.028
We thank C.A. Cansler for advice on study design, field, and laboratory assistance, and comments on earlier versions of this paper. We thank L. Brett for field assistance. J. Meyer and Yosemite National Park provided logistical support. M. Barth, P. Chi, C. Maher, and D. Wright provided valuable comments on previous versions of this manuscript. A.T. Gabrielson was supported by a College of Forestry and Conservation Irene Evers’ Undergraduate Research Scholarship and a University of Montana Davidson Honors College Undergraduate Research Award. Two anonymous reviewers and the associate editor provided sets of detailed comments and suggestions for revision that markedly improved the original manuscript.
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Gabrielson, A.T., Larson, A.J., Lutz, J.A. et al. Biomass and Burning Characteristics of Sugar Pine Cones. fire ecol 8, 58–70 (2012). https://doi.org/10.4996/fireecology.0803058
- fuel loading
- Pinus lambertiana
- Sierra Nevada
- surface fuel
- Yosemite National Park