- Research Article
- Open Access
Landscape-Scale Vegetation Change Following Fire in Point Reyes, California, USA
Fire Ecology volume 7, pages 114–128 (2011)
Fire is an important factor in determining plant community composition and distribution. This study quantifies landscape-scale vegetation change following a large fire at Point Reyes National Seashore, California, USA. Vegetation in the Point Reyes region is characterized by a complex mosaic of grassland, shrub, and forest plant communities, and by high levels of plant diversity. Although large fires are relatively rare on the coast of California north of San Francisco Bay, they are important in determining the distributions of plant communities at the landscape scale. We mapped vegetation communities throughout the study area using aerial imagery and analyzed how vegetation shifted following fire. We found substantial areas had transitioned from coastal scrub to ceanothus scrub (Ceanothus thyrsiflorus Eschsch.) or Bishop pine (Pinus muricata D. Don) forest following fire. Transitions from shrub to tree vegetation following fire have rarely been documented in this region. Logistic regression analysis was used to examine the factors influencing the post-fire distribution of Bishop pine and ceanothus scrub. Proximity to pre-fire Bishop pine stands and pre-fire vegetation type were the most important predictors of post-fire Bishop pine regeneration. Pre-fire vegetation type, burn severity, and topography were the most important predictors of post-fire ceanothus scrub distribution. This study demonstrates the capacity of these ecosystems for substantial change over short time periods in response to fire, and identifies some of the factors driving this change.
Fire is one of the primary processes shaping landscape-scale vegetation patterns in western North America. Variations in the frequency, intensity, seasonality, and spatial scale of fire strongly influence patterns of plant community regeneration (Turner et al. 1997, Agee 1998, Romme et al. 1998, Rundel et al. 1998, Brown et al. 1999, Sugihara et al. 2006, Potts et al. 2010). The role of fire in creating landscape-scale heterogeneity has been well documented in certain ecosystems such as the lodgepole pine (Pinus contorta Douglas ex Louden) forests of the Rocky Mountains (Schoennagel et al. 2008) and pine and mixed conifer forests of the southwest US, Sierra Nevada, and northwestern Mexico (Fulé et al. 2002, Stephens et al. 2008, Collins and Stephens 2010). At the landscape scale, plant communities in this region shift both spatially and temporally in response to processes such as a fire, grazing and succession.
The ecosystems of coastal northern California have high levels of both alpha and beta diversity (Whittaker 1972, Barbour et al. 2007, Thorne et al. 2009, Kraft et al. 2010). Many of the plant species and communities in this region are rare, due to the unique environment and biogeographic history and to human impacts such as urbanization and invasive species (Axelrod 1958, Davis and Borchert 2006, Seabloom et al. 2006). Some of these species and communities depend upon fire in order to persist. At the landscape scale, plant communities in this region shift both spatially and temporally in response to fire and disturbances such as grazing and to biotic interactions via processes such as succession (McBride and Heady 1968, McBride 1974, Callaway and Davis 1993, Keeley 2005).
The fire ecology of this region is complex. Plant communities are comprised of a mix of fire dependent and fire neutral species (Stuart and Stephens 2006). The fire history of coastal northern California has varied over time with periods of high fire frequency during the Native American and early rancher eras, and lower fire frequency prior to Native American management and again in recent times (Menzies 1793, Greenlee and Langenheim 1990, Brown et al. 1999, Keeley 2002, Anderson 2005, Keeley 2005, Stephens et al. 2007). Given its high alpha and beta diversity, wide range of adaptations to fire, and historical shifts in fire frequency, this region provides a rich opportunity for exploring the role of fire in driving landscape-scale vegetation patterns.
As a result of the high diversity of this system, the response of plant communities to fire may be more complex than what has been documented in other vegetation types (e.g., Turner et al. 1994, Collins and Stephens 2010). Further, because fire is less frequent in northern coastal California than in many other areas of the western US, opportunities to observe the impacts of fire on landscape-scale heterogeneity in this region are rare. The majority of published literature on vegetation transitions associated with fire in coastal California ecosystems documents shifts from woody to herbaceous vegetation following fire, and is based on studies carried out at relatively small spatial scales (e.g., Zedler et al. 1983, Callaway and Davis 1993, Keeley 2005, Talluto and Suding 2008; W.K. Cornwell, University of California, Berkeley, unpublished review). One landscape-scale study from the central coast region of California found higher transition rates from scrub to grassland in areas that had burned, and shifts from grassland to scrub in unburned areas (Callaway and Davis 1993). There is a paucity of information in the literature documenting other types of transitions such as grassland to forest, grassland to shrub, or shrub to forest following fire (but see Davis et al. 2010).
The 1995 Vision Fire at Point Reyes National Seashore (PRNS), California, USA, provided a unique opportunity to examine landscape-scale shifts in vegetation in coastal ecosystems. This fire was the largest, by several orders of magnitude, at PRNS since it was established in 1962. It burned 5000 ha from 3 October through 8 October 1995. Approximately 4690 ha of the burn were within the boundaries of PRNS, which is more than 15 % of the total park area (Figure 1). Fires as large as the Vision Fire are rare in the highly urbanized areas of the northern California coast in the vicinity of PRNS. In addition, detailed vegetation maps were available from immediately prior to the burn. This study documents changes in post-fire vegetation in the Vision Fire burn area and examines how patterns of vegetation change are related to burn severity, topography, soils, and pre-fire vegetation.
Point Reyes National Seashore is located in coastal Marin County, California, USA, approximately 45 km north of San Francisco. It is a 28 751 ha peninsula, which is bounded on the northeast by the San Andreas Fault (Figure 1). The climate in the study area is Mediterranean with wet winters and cool, dry summers. Temperatures range from lows of 6 °C to 9 °C and highs of 18 °C to 24 °C during the summer months, to lows of 2 °C to 4 °C and highs of 15 °C to 17 °C during winter. Average annual precipitation ranges from 50 cm near the coast to as much as 100 cm near the Bear Valley visitor center (Bear Valley Weather Station 1964–2010). Approximately eighty percent of the precipitation in the area occurs between November and March. Summer precipitation is low, averaging less than 0.5 cm per month. Summer months are characterized by coastal fog. Precipitation from fog drip has not been quantified for PRNS, but one study further north on the California coast (Requa, California) found summer fog drip provided an additional 22 cm to 45 cm of water annually (Dawson 1998). The most extreme fire weather generally occurs in October and November when high pressure systems over the Great Basin result in dry, hot Diablo winds blowing out of the east or northeast. The Vision Fire was started by a campfire on 3 October 1995 and, during the period of active fire growth, relative humidity dropped to 9 %, winds reached 35 km hr−1, and temperatures reached 28 °C (Marin County Fire Department, unpublished data).
The dominant plant communities in the study area are Bishop pine (Pinus muricata D. Don) forest, Douglas-fir (Pseudotsuga menziesii [Mirb.] Franco) forest, northern coastal scrub (dominated by coyote brush, Baccharis pilularis DC), blue blossom ceanothus (Ceanothus thyrsiflorus Eschsch.) scrub, and northern coastal prairie (dominated by a mix of native and non-native, annual and perennial, grass species). Bishop pine forest and ceanothus scrub both depend on fire in order to persist. The dominant species of Douglas-fir forest, northern coastal scrub, and northern coastal prairie are all able to tolerate fire but do require fire to reproduce. This analysis focused on post-fire change in the distribution of Bishop pine and blue blossom ceanothus, because these two species changed in distribution and extent most dramatically following the fire.
In 2003, a detailed vegetation map was finalized for PRNS following both the California Manual of Vegetation and the National Vegetation Classification systems (Sawyer and Keeler-Wolf 1995, Grossman et al. 1998, Schirokauer et al. 2003). This vegetation map was based on 1994 imagery and therefore reflects the vegetation communities present prior to the 1995 Vision Fire. The results presented here use vegetation classified to the “vegetation management community” as defined in the PRNS Plant Community Classification and Mapping Project Final Report (Schirokauer et al. 2003). The vegetation management communities present in the study area were Bishop pine forest, Douglas-fir forest, hardwood forest, riparian forest and shrubland, coastal scrub, blue blossom ceanothus scrub, grassland, and herbaceous wetland.
Vegetation Mapping and Accuracy Assessment
We mapped vegetation after the Vision Fire using color digital orthophoto quarter quadrangle images (1 m resolution), which were collected in March and April 2004 (County of Marin 2010). These images were supplemented by the National Agricultural Imagery Program aerial photography (1 m to 2 m resolution) from August 2005 (USDA Forest Service 2009). Polygons were mapped to the same vegetation management community types on field reconnaissance data and expert knowledge of PRNS vegetation communities. A “heads-up digitizing” approach was used based on the recommendation of the California Department of Fish and Game Vegetation Classification and Mapping Program (Keeler-Wolf 2007). To maximize consistency with the existing vegetation map, the minimum mapping unit used was 0.5 ha (Schirokauer et al. 2003).
Accuracy assessment of the hand-digitized polygons was conducted using 206 accuracy assessment plots, which were installed in 1998 and 1999, after the Vision Fire, inside the fire perimeter. Plots were randomly located and were 0.5 ha in size. At each plot, percent cover was determined for each species with >1 % cover, and height class and percent cover were estimated by life form (Schirokauer et al. 2003). Although the plot data were collected five to six years before the date of the imagery used for vegetation mapping, changes over this period were likely limited to changes in vegetation stature, minor shifts in species composition, or successional changes over small areas. The broad vegetation community classes used for this analysis are relatively stable over short time frames in the absence of large scale fire and disturbance (Point Reyes National Seashore, Fire Effects Monitoring Program, unpublished data).
The accuracy assessment used both the widely accepted confusion matrix and kappa coefficient approaches (Congalton et al. 1983, Congalton 1991, Foody 2002). The confusion matrix approach depicted the mapped vegetation communities in each row and the field-observed vegetation communities from the accuracy assessment plots in each column. The mapped vegetation type of each accuracy assessment plot was listed in the appropriate row. From this “producer’s accuracy,” or percentage of a particular vegetation class that had been correctly mapped as that vegetation class, and “user’s accuracy,” or the percentage of a mapped class that was mapped correctly, were both calculated (Congalton 1991). The kappa statistic was also calculated as an indicator of accuracy, which accounted for any correct classification that was due to chance (Lillesand et al. 2004).
Vegetation change between the 1994 and 2004 images was quantified by calculating the percentage change in area from pre- to post-fire in each vegetation class. Additionally, spatially explicit vegetation change was calculated and a transition matrix and diagram were constructed using raw area measurements (Mouillot et al. 2005).
Logistic regression analysis was used to examine the patterns driving vegetation change following fire. Specifically, analysis focused on post-fire presence or absence of Bishop pine and ceanothus scrub as response variables because those vegetation types experienced the greatest change following fire. In building logistic regression models, we considered the following predictor variables: slope, aspect, elevation, soil type, pre-fire vegetation type, burn severity, and, for analyses of Bishop pine, distance from pre-fire Bishop pine stands. Slope, aspect, and elevation were all based on digital elevation model data, which were resampled to 30 m × 30 m pixels. Soil type data came from the Marin County Soil Survey (USDA 1985). Pre-fire vegetation data came from the PRNS vegetation map described above (Schirokauer et al. 2003). Landsat-based differenced normalized burn ratio data were used as the metric of burn severity. The normalized burn ratio (NBR) was calculated from Landsat bands 4 and 7, and the differenced NBR (dNBR) was the post-fire NBR subtracted from the pre-fire NBR (Key and Benson 2006). The dNBR data for the Vision Fire were obtained through the Monitoring Trends in Burn Severity program, which provides burn severity data using dNBR methodology for all large fires in the United States dating back to 1984 (Eidenshink et al. 2007). Soils and vegetation layers were converted from vector to 30 m × 30 m raster format. All GIS analyses used ArcGIS version 9.3 (Environmental Research Institute, Redlands, California, USA) with standard extensions.
The initial data set included all pixels in the study area for a total of 51 101 observations. Semivariograms were constructed to explore patterns of spatial autocorrelation in the data (Rossi et al. 1992, O’Sullivan and Unwin 2002). Based on the semivariograms, which showed spatial autocorrelation up to 200 m, the data were randomly subsampled so that all data points were a minimum of 200 m apart. This resulted in a dataset of 346 observations, which was used for all subsequent analyses. Data were analyzed using logistic regression, and all parameters were tested for normality and heteroscedasticity. Models initially included all variables, and those with significant effects (P < 0.05) in the initial model were selected for inclusion in the final model. Likelihood-ratio tests were used to compare the full versus reduced models. All statistical analyses were completed using the R statistical software version 2.11.1 (R Development Core Team 2009).
The accuracy assessment is summarized in Table 1; overall mapping accuracy was 79 %. The producer accuracy, or percentage of field plots that were mapped correctly, ranged from a high of 91 % for the Bishop pine community type to a low of 56 % for the hardwood community type. The producer accuracy for Bishop pine, blue blossom ceanothus, and coastal scrub, which collectively comprise 75 % of the study area, ranged from 83 % to 91 %. User accuracy, or percentage of the mapped areas that corresponded with field plots of the same vegetation type, ranged from 90 % for herbaceous wetland to 70 % for grassland. For Bishop pine, blue blossom ceanothus, and coastal scrub, the user accuracy ranged from 72 % to 87 %. The kappa coefficient for the overall classification was 0.75.
Changes in vegetation are summarized in Table 2. The largest change was in ceanothus, which increased by 844 ha, or more than 4000 %. Bishop pine increased by 360 ha, or 85 %. The largest decreases were in coastal scrub, which was reduced by 672 ha, or 27 %, and Douglas-fir, which decreased by 386 ha, or 46 %.
Vegetation changes were examined more closely by looking at spatially explicit shifts in vegetation community (Figure 2). Figure 3 shows a transition diagram of major vegetation types from pre-fire vegetation to post-fire vegetation. Table 3 depicts transitions among all vegetation types. There were substantial shifts not only in the overall area of each vegetation community, but also in the distribution of these communities across the landscape. In the case of Bishop pine, only 240 ha, or approximately 60 %, of the area of Bishop pine present before the fire returned to Bishop pine after the Vision Fire. Much of the Bishop pine present post-fire was growing in areas that were formerly coastal scrub. Blue blossom ceanothus also made significant incursions into areas of former coastal scrub and Bishop pine forest.
Based on logistic regression models, distance from pre-fire Bishop pine stand and pre-fire vegetation type were significant predictors of Bishop pine presence or absence (Table 4). The probability of Bishop pine occurrence decreased with increasing distance from pre-fire Bishop pine stands (Figure 4). The saturated model for Bishop pine did not provide a better fit than the final model, which included only distance from pre-fire Bishop pine stand and pre-fire vegetation type (P = 0.315). For blue blossom ceanothus distribution, pre-fire vegetation type, burn severity, slope, and elevation were all significant predictors in the final model (Table 5). The probability of ceanothus occurrence increased with increasing burn severity and slope, and decreased with increasing elevation (Figure 4). Again, the saturated model did not provide a better fit than the final model (P = 0.380).
Mapping and Accuracy Assessment
Overall map accuracy was good and was comparable to that of the original mapping effort. Over 5 % of the overall mapping error resulted from areas classified based on the field data as coastal scrub that were subsequently mapped as Bishop pine. Informal examination of these areas revealed that they were coastal scrub with a low density Bishop pine component (15 % to 20 % Bishop pine cover). Because these trees will undoubtedly increase in ecological importance as they grow and expand their canopies, it is preferable to consider areas of open growing Bishop pine as Bishop pine rather than coastal scrub.
Bishop pine forest changed both in extent and distribution following the Vision Fire. Not only did Bishop pine extent nearly double, but the distribution of Bishop pine forest shifted from being restricted to ridge tops pre-fire to extending from the ridges all the way down to the Pacific coast post-fire. It should be noted that there were isolated individual Bishop pine trees present in areas closer to the Pacific coast prior to the fire; the change we describe refers to the distribution of the Bishop pine community. Bishop pine expansion following fire is not surprising given the autecology of this species. Bishop pine is serotinous and is adapted to high severity stand replacement fires (Sugnet and Martin 1984, Stuart and Stephens 2006). Because the Vision Fire burned through pre-fire Bishop pine forest with high intensity, we are confident that the vast majority of areas mapped as Bishop pine following the fire regenerated from seed post-fire.
Logistic regression models revealed that the best predictors for post-fire Bishop pine regeneration were whether the pre-fire vegetation was dominated by Bishop pine and proximity to pre-fire stands of Bishop pine. The occurrence of post-fire Bishop pine stands drops off dramatically beyond distances of 1 km from pre-fire Bishop pine stands. Bishop pine seedlings predominantly established in areas that were dominated by Bishop pine and coastal scrub pre-fire. Some areas of pre-fire grassland were converted to Bishop pine post-fire. Seed dispersal, which is mainly wind driven, was likely the primary factor determining where Bishop pine regeneration occurred. Dispersal by small mammals may also occur, but the impacts of small mammals on Bishop pine distribution are not clear. The presence of suitable mycorrhizal symbionts may also be an important factor in post-fire Bishop pine establishment (Baar et al. 1999). Similar expansion of closed cone pine species following fire has been observed in other parts of California (S. Fritzke, National Park Service, personal communication).
Blue blossom ceanothus also changed drastically in its extent following the Vision Fire. Although scattered individuals were present pre-fire, the sort of dense, expansive stands described in this study were absent before the fire. Species in the genus Ceanothus exhibit a wide array of life history strategies, including sprouting or reproducing only from seed following fire (Keeley and Zedler 1978). At PRNS, blue blossom ceanothus exhibits an obligate seeding strategy, but there is evidence that other populations of this species may produce basal sprouts following fire (Fross and Wilken 2006; T. Parker, San Francisco State University, personal communication). The buried seed bank that germinated following the Vision Fire had likely been left by a previous post-fire population of ceanothus that had senesced prior to the initial vegetation mapping effort due to age-dependent mortality.
Based on logistic regression models, blue blossom ceanothus established in lower elevation, high burn severity areas with steep slopes. Similar to Bishop pine, most of this expansion was into areas that had been previously dominated by coastal scrub. Coyote brush may be less likely to follow high intensity fire due to limited sprouting and seedling establishment.
There is mixed evidence regarding the impact of burn severity on vegetation recovery following fire. The importance of burn severity varies with vegetation type and the aspect of post-fire vegetation being studied (e.g. Turner et al. 1999, Keeley et al. 2005, Franklin et al. 2006, Keeley et al. 2008). Our study found a significant positive relationship between burn severity and post-fire ceanothus distribution, which is consistent with other studies (Moreno and Oechel 1994, Keeley et al. 2005). The lack of evidence for the importance of burn severity in determining Bishop pine distribution is inconsistent with the findings of Turner et al. (1999) in lodgepole pine forests. However, studies in chaparral have found that burn severity is relatively unimportant in determining post-fire vegetation recovery, especially over the longer term, as long as fire intervals are long enough for seedbank accumulation (Keeley et al. 2005, Keeley et al. 2008).
The mosaic of plant communities at Point Reyes National Seashore has undoubtedly been shifting over time and space for thousands of years due to climate, successional processes, lightning fires, burning by Native Americans, herbivory, and ranching (Anderson 2005). The Vision Fire is an example of an ecological event that caused major changes in the landscape-scale patterns of PRNS vegetation communities. This study provides direct quantitative evidence for the changes that can occur following fire, and provides a unique example of post-fire vegetation transitions from grassland to forest, and from shrub to forest.
In addition to providing evidence for vegetation transitions that have not commonly been observed and documented in the literature for this region, this study also demonstrates that multiple successional pathways are possible following fire in this ecosystem (i.e., a given pre-fire vegetation type has the potential to shift to any number of vegetation types following fire). Many studies have found evidence for multiple successional pathways following fire, although, to our knowledge, few of these studies have focused on the ecosystems of northern coastal California (for an example from the central coast of California, see Callaway and Davis 1993). In our study, coastal scrub was probably the most dynamic vegetation type: transitions to grassland, ceanothus scrub, and Bishop pine, as well as self-replacement, all occurred following fire. Some of the changes we documented, such as the shift from Douglas-fir forest to blue blossom ceanothus, will not persist over the long term. These areas will likely shift back to their pre-fire state in the absence of another fire. Other changes, such as the transition from coastal scrub to Bishop pine forest, are more likely to persist over long time periods and represent fire-meditated shifts to alternative states. Many possible causes for multiple successional pathways have been proposed, including disturbance history, vegetation composition at the time of disturbance, topography, burn intensity, buried and aerial seed sources, soils, and stochastic factors (Abrams et al. 1985, Fastie 1995). Vegetation composition prior to fire, topography, burn intensity, and seed source availability, as well as stochastic factors, were likely the most important determinants of successional pathways following the Vision Fire.
Understanding these landscape-scale vegetation dynamics is interesting from a theoretical perspective and important for management. Few ecosystems are so plastic in their response to fire and in the spatial variability of the vegetation composition over relatively short time frames. For managers, it is important to understand how processes such as fire can dramatically shift the distribution of different vegetation types along with the suite of wildlife species that those vegetation communities support.
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We would like to thank the Point Reyes National Seashore natural resource and fire management staff for support in making this project happen. In addition, we would like to thank K. Peay for initial inspiration and M. Lahiff and K. Peay for assistance with statistical analyses.
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Forrestel, A.B., Moritz, M.A. & Stephens, S.L. Landscape-Scale Vegetation Change Following Fire in Point Reyes, California, USA. fire ecol 7, 114–128 (2011). https://doi.org/10.4996/fireecology.0702114
- Ceanothus thyrsiflorus
- coastal California plant communities
- fire effects
- landscape ecology
- multiple successional pathways
- Pinus muricata
- vegetation dynamics