A simple metric of landscape fire exposure

Abstract

Context

Proximity of landcover elements to each other will enable or constrain fire spread. Assessments of potential fire propagation across landscapes typically involve empirical or simulation models that estimate probabilities based on complex interactions among biotic and abiotic controls.

Objectives

We developed a metric of landscape fire exposure based solely on a grid cell’s proximity to nearby hazardous fuel capable of transmitting fire to its location. To evaluate accuracy of this new metric, we asked: Do burned areas occur preferentially in locations with high exposure?

Methods

We mapped exposure to hazardous fuels in Alberta, Canada using a neighbourhood analysis. Correspondence between exposure and 2331 fires that burned 2,606,387 ha following our 2007 assessment was evaluated and exposure changes between 2007 and 2019 were assessed.

Results

In all eleven ecological units analysed, burned area surpluses occurred where exposure was ≥ 60% and corresponding deficits occurred where exposure was < 40%. In seven ecological units, the majority of burned areas had pre-fire exposure ≥ 80%. Between 2007 and 2019, land area with exposure ≥ 80% increased by almost a third.

Conclusions

Exposure to hazardous fuels is easily quantified with a single thematic layer and aligns well with subsequent fires in Boreal, Foothills and Rocky Mountain natural regions. The resulting fire exposure metric is a numeric rating of the potential for fire transmission to a location given surrounding fuel composition and configuration, irrespective of weather or other fire controls. Exposure can be compared across geographic regions and time periods; and used in conjunction with other metrics of fire controls to inform the study of landscape fire.

Introduction

In fire-prone ecosystems, the pattern of different vegetation types, stand-ages, burned areas, and non-fuel creates landscape heterogeneity that modulates fire behaviour (Turner and Romme 1994; Peterson 2002; McKenzie et al. 2011). Spatial arrangement of vegetation and other cover types are considered bottom-up (endogenous) controls on fire propagation that interact with top-down (exogenous) controls such as long-term climatic patterns and weather conditions (Simard 1991; Falk et al. 2007; McKenzie et al. 2011; Newman et al. 2019). The study of how neighbouring landscape elements interact with each other and with overlying ecological processes is a central concern in landscape ecology that has motivated development of quantitative landscape metrics for describing the physical expression of pattern-process dynamics (White 1987; Turner 1989; Pickett and Cadenasso 1995; Walz 2011; Gustafson 2019). Measures of landscape contagion and resistance are used to quantify the structural characteristics of landscapes that either facilitate or constrain the movement of an agent or process (Newman et al. 2019). In the case of habitat fragmentation and the movement of organisms, metrics of contagion can be used to measure the configuration and aggregation of landscape elements based on cell-adjacencies calculated from a single thematic layer of cover types (e.g., O’Neill et al. 1988; Turner 1989; Li and Reynolds 1993; McGarigal and Marks 1995; Riitters et al. 1996). Landscape analysis of potential wildfire movement is complicated by interacting biotic and abiotic controls on fire processes that have spawned complex empirical and simulation modelling frameworks.

Historical fire edges have been used to study the influence of fire environment variables and anthropogenic factors on landscape fire resistance with binary predictive statistical models (e.g., Narayanaraj and Wimberly 2011; Holsinger et al. 2016; Macauley 2020) and machine learning methods (e.g., O’Connor et al. 2017; Rodrigues et al. 2020). Unfortunately, resulting predictive models do not provide a standardized and generalizable characterization of landscape fire that can be applied across large areas, due to spatial and temporal non-stationarity in the underlying statistical relationships and historical data that is often incomplete, inconsistent or unreliable over broad areas. Simulation models offer an alternative framework for exploring the potential for fire movement across landscapes using a variety of approaches reviewed by Perry (1998) and Papadopoulos and Pavlidou (2011).

Widely used fire growth models like FARSITE (Finney 2004) and Prometheus (Tymstra et al. 2010) simulate the deterministic movement of an individual fire using fire environment inputs that describe fuel, weather and topographic conditions. These models of discrete fire events are extended to landscape assessments with Monte Carlo simulations such as FSim (Finney et al. 2011) and Burn-P3 (Parisien et al. 2005) that model the spread of multiple fires from stochastic ignitions and weather in large numbers of repeated iterations to calculate the probability of a grid-cell burning. Simulated burn probability maps have been used to explore the influence of landscape configuration and fuel discontinuities on fire spread across natural landscapes (e.g., Beverly et al. 2009; Ager et al. 2012; Stockdale et al. 2019) as well as theoretical landscapes generated with varying configurations (e.g., Finney 2007; Parisien et al. 2010). Despite their popularity, simulated burn probability maps have exhibited poor alignment with subsequent observed wildfires and may not be informative in regions characterized by infrequent fire and low probabilities of burning (Beverly and McLoughlin 2019). Alternate simulation frameworks exist for modelling the movement of fire across raster landscapes (e.g., Finney 2002, 2006; Gray and Dickson 2015; Conver et al. 2018); however, all models that simulate fire spread must account for highly stochastic abiotic controls on fire, such as ignition locations and weather, which introduce numerous data requirements, computational complexities, and accumulated uncertainty.

Rapid expansion of landscape fire simulation modelling in the 1990s coincided with a broader trend towards increasingly complex and data-intensive approaches for representing multifaceted ecological processes in landscape models (Larsen et al. 2016; Getz et al. 2018). Perera et al. (2015) note the lack of consensus among ecologists about the desirability of simple, parsimonious models versus complex simulations of disturbance processes. The question of appropriate model complexity has been largely ignored by wildland fire modelers, despite it being a topic of high importance in other ecological disciplines (e.g., Murray 2007; Collie et al. 2016; Larsen et al. 2016; Getz et al. 2018; Baartman et al. 2020). A modeler seeking basic explanation is advised to retain only essential, first-order processes (Murray 2003, 2007). According to Gustafson (2013), modelers should “simulate processes at the most fundamental level that is reasonable, while avoiding the temptation to add unnecessary detail just because it is feasible.”

Simple relative ratings of fuel moisture and potential fire behaviour (i.e., Van Wagner 1987) based solely on weather measurements irrespective of fuel conditions have long been used to characterize ecological fire processes (e.g., Flannigan and Harrington 1988; Flannigan et al. 2005) and for supporting fire management decisions (Cunningham and Martell 1973; Martell et al. 1987; Wotton and Martell 2005). Comparable fuel-based metrics formulated irrespective of weather have yet to be fully explored, possibly due to the widespread availability and appeal of sophisticated fire growth and simulation modelling frameworks. In this study, we sought to develop a simple landscape metric of fire based solely on stable physical fuel properties decoupled from highly dynamic abiotic controls on fire propagation, notably ignition patterns and weather, which fluctuate over divergent temporal horizons (e.g., minutes, hours and days).

Wildfire propagation will depend in part on the position of flammable landscape elements in relation to each other. Fires spread in a contagious endothermic–exothermic chain reaction that only persists if heat from burning vegetation is successfully transferred over a distance to preheat and ignite adjacent or nearby fuels (Rothermel 1972; Van Wagner 1983; van Wagtendonk 2006). The transmission of fire from one location to another occurs over relatively localized distances associated with wildfire heat transfer mechanisms that include direct contact with flames, radiant heat, and embers (Countryman 1977; Sullivan 2017). In northern forest ecosystems, embers transported by a convective column can transmit fire to locations several kilometres away (MNP 2017); however, empirical observations (e.g., Page et al. 2019) and theoretical models (e.g. Albini 1979) suggest fire transmission from embers occurs predominantly within 500 m, except under the most extreme conditions. Following this simple reasoning, Beverly et al. (2010) used ember distance ranges and the concept of exposure to assess potential wildfire movement into the built-environment based solely on the proximity of a location to nearby hazardous fuels.

Exposure is defined as the extent to which a value, resource, asset or geographic area may be subject to or come into contact with a potential source of harm (ISO 2009; Thompson et al. 2016). A potential source of harm may relate to the process itself (i.e., an actively burning wildfire is the hazard) or the preconditions necessary for that process to occur, in which fuels are the hazardous condition that can result in a wildfire (Hardy 2005). Exposure assessments typically characterize the juxtaposition of values, such as built structures, with geographic locations where burning is possible (e.g., Beverly et al. 2010) or probable (e.g., Haas et al. 2013; Whitman et al. 2013); however, the concept is equally relevant to the transmission of fire from hazardous fuel to nearby flammable vegetation.

Exposure is not an event whose probability of occurrence can be estimated, but rather it is a physical quantity whose value at any point in time and space can be measured. We adapted the exposure method developed by Beverly et al. (2010) to map exposure to hazardous fuels in Alberta, Canada using a neighbourhood analysis. Exposure was estimated for a landscape grid at the cell level by the proportion of neighbourhood cells that contain hazardous fuel types. The resulting exposure metric describes the extent to which land cover type in the vicinity of a location will either contribute to or resist fire transmission to that location. The approach explicitly accounts for the contagious nature of combustion without the need for time- and data-intensive simulations of fire growth. To evaluate model performance, we assessed correspondence between exposure mapped for the 2007 assessment year and subsequent observed burned areas and compared results among eleven ecological units within the study area. We hypothesized that most burned areas would occur in locations with exposure ≥ 60%, and that fire deficits would prevail in locations with exposure < 40%. To test the robustness of the approach, we estimated five alternative formulations of the exposure metric in which we varied the size of the focal fuel neighbourhood and introduced weighting schemes to represent within-neighbourhood differences in fuel configuration, fuel load, and potential fire behaviour. Implications of our results for landscape fire ecology, fire management and future research are discussed.

Methods

Study area

Exposure to hazardous fuels was assessed for the entire Forest Protection Area (FPA) of the province of Alberta; an area spanning approximately 39 million hectares. Eleven ecological units within the study area were defined by Natural Region and Natural Subregion boundaries (Natural Regions Committee 2006) (Fig. 1). The Rocky Mountain Region was analysed as a single unit, owing to the limited spatial extent of observed burned areas in that region. All other ecological units consisted of interlocking Natural Subregions. The Peace-Athabasca Delta subregion was omitted from analysis due to its small size and lack of observed burned areas. Fire regime characteristics by ecological unit are summarized in Online Appendix A. Descriptions of climate, vegetation, topography, geology, soils and hydrology within each ecological unit are detailed in the reference report Natural Regions and Subregions of Alberta (Natural Regions Committee 2006).

Fig. 1

Location of the study area and ecological units within the Forest Protection Area (FPA) of the province of Alberta, Canada

Data

Thematic land cover maps in a raster format with a 100 m × 100 m resolution were obtained for the years 2007, 2016 and 2019 from the Alberta Wildfire Management Branch. Non-fuel cover-types included water and barren ground; areas disturbed by wildfires or harvesting that are subject to reclassification with time since disturbance; and anthropogenic features such as roads. Flammable cover types were classified according to the standard fuel types used in Canadian fire behavior models (i.e., Forestry Canada Fire Danger Group 1992). Cover type was derived from agency-defined rules applied to three main sources: the Alberta Vegetation Inventory (AVI), 69–72% of the study area; Alberta Ground Cover Classification (AGCC), 18–21%; and disturbance inventories compiled by the provincial government, 8–11%. A small portion (i.e., 2%) of the 2007 fuel map was informed by two photo-based forest inventories from the mid-1980s and early 1990s.

AVI is updated every 10–15 years and specifies hydrography, vegetation cover types and stand structure attributes from interpreted aerial photographs (Resource Information Management Branch 2005) with a minimum polygon size of 2.0 ha, considered valid for use at a scale of 1:20,000. AGCC is derived from Landsat TM5 and TM7 satellite imagery that was last updated in 2000. Land cover is assigned to one of 99 classes describing anthropomorphic features, vegetated uplands, wetlands, water, and barren land at a 30 m × 30 m resolution considered useful at a 1:50,000 scale (Sánchez-Azofeifa et al. 2004). Disturbance inventories are updated annually and consist of polygon boundaries associated with wildfires, forest harvesting, and land clearing. Recently harvested cut blocks are generally interpreted from aerial photographs to a minimum polygon size of 0.5 ha and a 5 m level of precision (Resource Information Management Branch 2005). Wildfire polygons are mapped with a variety of methods including ground and airborne Global Positioning Systems (GPS), infrared scanning, digitized aerial photographs, satellite imagery classification, and hand-sketched boundaries. Wildfire polygons for the period 2007–2019 include fires that burned < 1.0 ha.

Metric estimation

We classified all conifer and mixedwood fuel types as hazardous fuels capable of transmitting fire within a 500 m distance range. Grid cells that contained these hazardous fuels were assigned a value of “1” and all other cells were deemed a non-hazard denoted by “0”. For exposure assessments in Boreal and Foothills Natural Regions of Alberta, Beverly et al. (2010) defined three exposure distance ranges (0–30 m, 0–100 m, and 100–500 m) to represent the spatial extent of different ignition mechanisms (i.e., radiant heat and the transport of short- and longer-range embers). We estimated exposure for a single, 500 m distance range compatible with our 1 ha resolution land cover raster.

Exposure to hazardous fuels was calculated for each cell in the landscape raster using the focal statistic tool of the ArcGIS Spatial Analyst toolset. We used a circular neighbourhood with a 5-cell (500 m) radius to sum the binary hazardous fuel grid across 80 cells that surrounded each assessment cell, excluding the assessment cell. Exposure was calculated as the focal statistic sum as a percentage of the maximum possible sum (i.e., of 80). By default, the modelling process generates exposure values for all cells in the land cover raster, including non-fuel cells such as rock, water and recently burned lands that are incapable of sustaining combustion, which were therefore discarded prior to further analysis. Exposure values within 500 m of the study area boundary were also discarded to remove edge-effects.

We estimated exposure to hazardous fuels for three time periods using land cover thematic layers representative of conditions during the 2007, 2016 and 2019 fire seasons. To validate our metric, all available fire polygons between 2007 and 2019 were compiled from the previously described provincial fire disturbance inventory. A total of 2331 fire perimeters encompassing 2,606,387 ha of observed burned areas were used to assess performance of the 2007 pre-fire exposure map. We expected distributions of exposure values in observed burned areas to be skewed towards the high-end of the range of values. Model accuracy was assessed based on an expectation that the majority of observed burned areas would have pre-fire exposure ≥ 60%.

To assess the metric’s discrimination ability, we used Chi squared tests to detect significant differences between the proportion of observed burned areas with exposure ≥ 80% and ≥ 60% compared with the corresponding proportion across the study area as a whole (i.e., the null model). Distributions of exposure values in burned and unburned areas were compared with a Wilcoxon rank sum test. Due to the presence of spatial autocorrelation in the data, we used a random sample of exposure values consisting of a 0.005 portion of the area under assessment to test for significant differences.

Following Beverly et al. (2010), we assumed that all hazardous fuel cells contribute equally to exposure, irrespective of differences in fuel type or configuration within the circular fuel neighbourhood. To account for the possible effect of reduced ember transmission with increasing distance from burning vegetation, we generated a distance-weighted exposure metric with a negative exponential decay function (Eq. 1):

$$y = 15.197e^{ - 0.01x}$$

(1)

where y is the weight given to a grid cell that contains a hazardous fuel, x is the distance (m) of the hazardous fuel cell from the grid cell under assessment, 15.197 is the value at distance 0 (i.e., the intercept), and the decay rate, λ = 0.01, is the inverse of the average distance between two cells in the grid (i.e., the raster resolution, 100 m). In the distance-weighted formulation of the exposure metric, the negative exponential spatial weight matrix was applied to the binary hazardous fuel grid prior to calculating the focal neighbourhood sum for each grid cell. The maximum possible sum of the weighted fuel neighbourhood was equivalent to that of the unweighted formulation (i.e., 80).

To account for possible effects of fuel type and fuel load on the transmission of fire from one cell to another, we estimated exposure weighted by variations in fuel attributes relevant to fire behaviour: crown fuel load (kg m⁻²), head fire intensity (kW m⁻¹), and rate of spread (m min⁻¹). Fuel attributes by fuel type and associated weights applied to the binary hazardous fuel layer are shown in Table 1. Crown fuel load is the standard load assigned to each fuel type in the Canadian Forest Fire Behaviour Prediction (FBP) System (Forestry Canada Fire Danger Group 1992). Head fire intensity and rate of spread by fuel type were calculated using FBP System equations and fire weather inputs representing 95th percentile conditions, which were derived from a database of almost 20,000 fires in Alberta between 2006 and 2018. In a final variant of the standard exposure metric, we used a 1000 m circular neighbourhood to test our assumption that fire transmission from one location to another was effectively represented by a 500 m circular neighbourhood.

Table 1 Fuel attributes and associated weights by fuel type used to calculate three variants of the exposure metric

Large fires > 1000 ha were responsible for 97% of observed burned areas in our study area, which is consistent with dominant Canadian fire regimes where infrequent, high intensity crown fires are typical (Stocks et al. 2002). To assess the sensitivity of the exposure metric to fire size, we compared distributions of exposure values in observed burned areas produced by fires in three different size classes: ≤ 100 ha, 100.1–1000 ha and > 1000 ha. We also investigated changes in exposure between 2007 and 2019 and estimated exposure for the 2016 assessment year in the vicinity of the community of Fort McMurray, which was heavily impacted by the Horse River Fire later that same year. To illustrate the unique landscape qualities expressed by the exposure metric, pre-fire exposure for Fort McMurray was then compared with simulated burn probabilities generated with the Burn-P3 model for the same year and location in a prior study (i.e., Beverly and McLoughlin 2019).

Results

Comparisons of exposure values in burned areas with those across the study area as a whole (i.e., the null model) indicated good discriminatory ability with the standard formulation of the metric (Table 2). Burned area surpluses in the study area were associated with exposure ≥ 60% and burned area deficits with exposure < 40%. None of the five alternative formulations of the exposure metric increased the magnitude of burned area surpluses (0.20) in high exposure areas and burned area deficits (− 0.18) in low exposure areas. All further analysis was therefore conducted with the standard formulation of the exposure metric with a 500 m fuel neighbourhood and an assumption that hazard fuels contribute equally to exposure, irrespective of their distance, fuel load or potential fire behaviour.

Table 2 Proportion of burned areas with high (≥ 60%) and low (< 40%) exposure values in relation to null model proportions for six different formulations of the exposure metric: the standard metric where hazard fuel grid cells contribute equally to exposure; four variants in which hazard fuel cells are weighted by either distance, fire behavior potential or fuel load; and one variant in which the circular neighborhood is increased to 1000 m

Exposure maps for the study area as a whole (Fig. 2) indicate the pattern of landscape fire exposure varies spatially across Alberta and revealed a marked escalation in landscape fire exposure between 2007 and 2019. In ten of eleven ecological units, the majority of observed burned areas had pre-fire exposure ≥ 60% and in seven of these units, the majority of burned areas had pre-fire exposure ≥ 80%. Between 2007 and 2019, land area with exposure ≥ 80% increased by almost a third. In all eleven ecological units analysed, burned area surpluses occurred where exposure was ≥ 60% and corresponding deficits occurred where exposure was < 40% (Fig. 3). Differences between observed and expected proportions of burned area with exposure ≥ 60% and ≥ 80% were significant in all ecological units (Table 3); however, the magnitude of these differences varied. Corresponding burned area deficits were consistently observed in locations where exposure was < 40%. In the Dry Mixedwood ecological unit, the burned area deficit was limited to locations with exposure < 20%.

Fig. 2

Exposure to hazardous fuels within the Forest Protection Area of the province of Alberta, Canada, for 2 years: 2007 and 2019

Fig. 3

Proportion of burned area (solid shaded bars) in each exposure class, by study area and ecological unit, versus proportions across the area as a whole (hollow dashed bars). BSA Boreal Subarctic, LBH Lower Boreal Highlands, NM Northern Mixedwood, KU Kazan Uplands, UF Upper Foothills, UBH Upper Boreal Highlands, RM Rocky Mountain, LF Lower Foothills, CM Central Mixedwood, AP Athabasca Plain, DM Dry Mixedwood

Table 3 Proportion of observed burned areas with hazard fuel exposure ≥ 80% and ≥ 60% compared with the corresponding proportion across the ecological unit as a whole (i.e., the null model) for two extents: (a) all burned areas; and (b) a random sample covering 0.005 of the burned area

The strength of evidence provided by distributions of exposure values in burned areas depends on the extent to which low exposure values are represented in the remainder of the area. For example, over 90% of the Athabasca Plain ecological unit had exposure ≥ 60%, such that a fire positioned randomly within its boundaries would align with high exposure values by default. In most other ecological units, a range of exposure values were represented and observed fires clearly selected for locations with exposure ≥ 60%. The lone exception was the Dry Mixedwood ecological unit, where most land area, as well as burned area, had exposure < 40%, suggesting that fire environment and fire regime attributes or possibly fuel data limitations in that ecological unit confounded results.

Mean exposure to hazardous fuels was significantly lower in unburned areas compared with burned areas (Online Appendix B). Average exposure across the study area as whole was 66.2% in burned areas and 49.7% in unburned areas. Within individual ecological units, excepting the Dry Mixedwood, average exposure to hazardous fuels within burned areas was 58–88% and median exposure was 61–95%. Average and median exposure to hazardous fuels in unburned areas were significantly lower, but varied substantially among ecological units and on their own offer little insight into metric performance. Exposure to hazardous fuels is not a probabilistic estimate. If exposure values are high in unburned areas, the metric is simply telling us that landscape configuration and composition is conducive to fire spread, should the opportunity for burning arise. In contrast, when large areas assessed as having predominantly high fire resistance (i.e., low exposure) are subsequently observed to burn, it suggests the exposure metric has not effectively characterised aspects of landscape configuration and composition relevant to fire propagation in that ecosystem.

Across the study area, excluding the Dry Mixedwood unit, only 6.5% of observed burned areas occurred in locations with exposure < 20%. In all ecological units, some low exposure locations subsequently burned, but this was generally limited to a small proportion of the total observed burned area. Three exceptions were the Dry Mixedwood, Central Mixedwood and Lower Foothills ecological units where 73%, 28% and 20% of burned areas respectively had ignition exposure < 40%. One third of these low-exposure burned areas were associated with a single large fire, the 2019 Chuckegg Creek Fire. This fire was also solely responsible for 92% of the low exposure areas that burned in the Dry Mixedwood ecological unit, where the metric performed poorly. Burned areas in locations assessed as having low exposure may be attributed to misclassification of land cover due to outdated inventory data or fuel conditions that do not conform well to the standard fuel types used to classify hazardous fuels. Observed burned areas in our eleven ecological units that were associated with ignition exposure < 40% occurred predominantly in deciduous and grass fuels.

Excluding the Dry Mixedwood ecological unit where the exposure metric performed poorly, 70% of burned areas occurred in locations with exposure ≥ 60%. Exposure values exhibited some sensitivity to fire size class (Fig. 4). The proportion of burned areas associated with exposure < 20% increased threefold from 0.06 to 0.18 as fire size-class was reduced from largest (> 1000 ha) to smallest (≤ 100 ha). Overall, fire size had a negligible impact on our results due to the extremely small proportion of burned areas (< 3%) associated with fires ≤ 100 ha.

Fig. 4

Distribution of exposure values in subsequently burned areas, by fire size class for the study area, excepting the Dry Mixedwood ecological unit

Exposure to hazardous fuels in the Fort McMurray area at the start of the 2016 fire season (Fig. 5) indicated the area was highly conducive to fire spread prior to the Horse River fire that destroyed over 3000 structures in the community later that same year. In contrast, burn probabilities simulated for the same location and year in a prior study (i.e., Beverly and McLoughlin 2019) indicated large continuous areas of low to moderate fire likelihood surrounded the entire community of Fort McMurray prior to the fire. Overall, our simple, univariate metric of exposure to hazardous fuels exhibited better alignment with subsequent real-world fires than burn probabilities generated with a complex landscape simulation model (Burn-P3) evaluated in a prior study (Beverly and McLoughlin 2019).

Fig. 5

Exposure to hazardous fuels for the 2016 assessment year in the Fort McMurray area of Alberta (left panel). Burn probabilities simulated with the Burn-P3 model by Beverly and McLoughlin (2019) for the same location and year. White hatch lines denote areas burned by the 2016 Horse River Fire (right panel)

Discussion

Metric performance

Observed burned areas between 2007 and 2019 in ten of eleven ecological units within our study area occurred predominantly in locations with ≥ 60% exposure to hazardous fuels. Burned area surpluses were consistently observed in these locations and corresponding deficits were consistently observed in locations with exposure < 40%. The sole exception was the Dry Mixedwood ecological unit, where our metric performed poorly; however, 92% of the burned area in low exposure areas in that unit were attributed to a single fire, which suggests possible anomalous conditions.

Comparisons of exposure estimated for 2007 and 2019 assessment years revealed a rapid escalation in landscape fire exposure. Over a relatively short 13-year time period, land area with exposure ≥ 80% increased by 30%. Some of this change may be an artefact of administrative updates to the fuel grid due to newly available data or changes in subjective decision rules used to classify existing data. Change in the fuel grid is expected to result from state transitions where recently disturbed areas assessed as non-fuel or non-hazardous fuel types transition to a hazardous fuel classification with the passage of time. Irrespective of the underlying source of change, additions of hazardous fuel to the land cover grid between 2007 and 2019 outpaced offsetting deletions that result primarily from new fire and harvest disturbances.

Robustness of the approach

To test the robustness of our fuel exposure metric, we estimated five alternative formulations in which we varied the size of the focal fuel neighbourhood and introduced weighting schemes to represent within-neighbourhood differences in fuel configuration, fuel load, and potential fire behaviour. None of these variants improved performance of our standard formulation in which a 500 m fire transmission neighbourhood is used and hazardous fuels within the neighbourhood are assumed to contribute equally to exposure irrespective of their configuration. This result is not surprising. Most of the area burned in Canada is caused by large fires ≥ 200 ha (Stocks et al. 2002) that burn under relatively uniform and generally very high to extreme fire weather conditions (Amiro et al. 2004). Large fires achieve most of their growth during a relatively small number of “spread event days” (Podur and Wotton 2011) when conditions are typically hot, dry and windy (e.g., Srock et al. 2018) and fuel moisture is uniformly low across large areas. Under these elevated fire weather conditions, we expect the minimum requirements for fire transmission within the 500 m distance range are being met in hazardous fuel types, regardless of the specific type of hazardous fuels present and regardless of the fuel load, fire intensity, rate of spread, or location of the hazardous fuel cell within the focal neighbourhood.

Fire size had an influence on model performance. When small fire polygons are used to extract exposure grid cells with a 1 ha resolution, a high proportion of error-prone edge pixels will result, which could explain declining metric performance with decreasing fire size-class. Declining performance for smaller fires could also be due to these fires burning under comparatively less-extreme conditions, such that shorter-range fire ignition processes become more influential. Fire size had a negligible impact on our results due to the extremely small burned area associated with small fires in our study area. Estimation of the exposure metric in ecosystems characterized by relatively small fire sizes will require finer-resolution land cover data than we used, to reduce the influence of potential edge-effects on results and to enable exposure assessments over shorter (i.e., ≤ 100 m) distance ranges.

Key assumptions

Our fuel-based exposure metric ignores information about topographic conditions, such as slope or aspect, which are known to influence fire behaviour. For a given fuel complex, slope can be expected to accelerate combustion and fire spread rates in comparison with flat terrain by enabling faster preheating of upslope fuels (van Wagtendonk 2006). Presence of complex topography in our study area was largely limited to the Rocky Mountain ecological unit, where the metric performed well. We suspect that slope and aspect have a minimal influence on the exposure metric due to the homogenized weather and fuel moisture conditions described above for large fires, such that locations exposed to hazardous fuel will burn, irrespective of the contribution of slope or other topographic variables towards combustion rates. While it was not a factor in our study area, further research will be necessary to explore the influence of weather, topographic conditions and other fire controls on metric performance in other fire regime contexts and geographic locations.

We used a 500 m fuel neighbourhood following Beverly et al. (2010). In that study, a literature review and theoretical model (i.e., Albini’s 1979) was used to define the distance range associated with ember transmission. Our results suggest the 500 m fuel neighbourhood was effective for assessing fire exposure within our study area. In other geographical areas, fire transmission may be driven by heat transfer mechanisms operating at different distance ranges, which could necessitate use of finer-resolution land cover data and may potentially explain the poor results in the Dry Mixedwood ecological unit.

Limitations of fuel data and fuel hazard classification

Exposure to hazardous fuels will reflect the resolution and accuracy of the land cover grid; and the subjective classification of these land cover types into a binary hazardous fuel grid. Fuel conditions in low exposure areas that burned provide some insight into the limitations of fuel data used in this study. For example, in the Central Mixedwood ecological unit, 65% of low exposure areas that burned were associated with aspen and grass fuels derived from inventory data > 15 years old and roughly one third of the low exposure areas that burned coincided with open peatlands. Boreal peatlands are known to resist fire spread when wet and conduct fire spread when dry (Thompson et al. 2019), such that classification as a hazardous fuel is dependent on drought conditions. Three quarters of the low exposure areas that burned in the Lower Foothills ecological unit were associated with prior disturbances in the form of harvest cutblocks (56%) and fires (19%). Previously burned or harvested areas are often designated as a grass fuel type for a period of time, which we considered a non-hazard for longer-range ember transmission, but these areas may actually contain sufficient regeneration to constitute a hazardous fuel classification. Likewise, we designated aspen stands a non-hazardous fuel that does not contribute to longer-range ember transmission, but these stands can sometimes have a well-developed spruce understory that has been shown to contribute to fire severity in Alberta (Greene et al. 2005), and would therefore constitute a hazardous fuel.

We expect enhanced land cover mapping would improve performance of the exposure metric as would use of underlying data sources to characterize hazardous fuels, such as the Alberta Vegetation Inventory and supplementary data sources in the form of wetland and ecosite mapping products. We opted to classify hazard fuels using FBP System fuel types following Beverly et al. (2010), primarily because these fuel types are well-known and understood by Canadian fire managers and researchers and are used in a wide range of fire research investigations and fire management tools. Fuel mapping capabilities are undergoing radical change due to new data collection methods including very high spatial resolution optical satellite data (e.g., Ahmed et al. 2018), airborne laser scanning (ALS) (e.g., Cameron 2020) and unmanned aerial vehicles (UAVs) combined with LiDAR (e.g., Shin et al. 2018; Fernandez-Alvarez et al. 2019) and computer image processing with machine learning (ML) methods (Guimarães et al. 2020). These new fuel data sources can be expected to generate more accurate hazardous fuel classifications in the future. Field visits to assess fuels in low-exposure areas that burned could potentially help to identify weaknesses and limitations in current fuel data and inform strategies for mapping hazardous fuels in the future.

Following Beverly et al. (2010), ignition exposure was assessed for combined spring and summer seasons. In that study, if a fuel type was considered a hazard in any season, it was classified as a hazardous fuel. Fuels such as grass and aspen are considered hazardous fuels during spring conditions, but only transmit fire over relatively short distances that were not represented by the coarse resolution of our land cover raster, and were therefore omitted. Assessments conducted at a finer spatial resolution could partition exposure by spring and summer, such that grass and aspen would be classified a hazardous fuel in spring but not summer.

Practical applications and relevance to fire risk assessment

Exposure to hazardous fuels can be assessed in minutes for large landscapes by one variable at virtually no marginal cost using rudimentary GIS techniques. Our landscape fire exposure metric is a numeric rating of the potential for fire transmission to a location given surrounding fuel composition and configuration, irrespective of weather or other fire controls. This simple, deterministic, univariate metric of fire exposure aligned well with real-world fires observed in our study area and represents a departure from computationally complex and data-intensive approaches for characterizing fire spread potential across landscapes.

Simple landscape fire metrics have received limited research attention, possibly due to a dominant fire risk modelling paradigm in which probabilistic assessments of fire likelihood are deemed compulsory. Thompson and Calkin (2011) define fire risk as a function of burn probability, conditional fire intensity, and fire effects. Similarly, recent reviews of wildfire risk assessment methods define fire risk as the combination of fire probability, fire behaviour and fire effects (Xi et al. 2019), or simply the product of fire probability and potential impact (Johnston et al. 2020). In landscapes where the likelihood of burning is low, such as the boreal forest, complex probabilistic modelling efforts may yield little insight into which locations can be expected to burn over the next or several years (Beverly and McLoughlin 2019). Flage et al. (2014) argue that probabilities are not well suited for characterizing the risk of rare events with potential catastrophic consequences and suggest alternatives such as possibilistic measures or qualitative methods in these cases.

The conceptual contribution of our exposure metric to landscape fire likelihood assessment is illustrated in Fig. 6. In probabilistic models of fire likelihood, the integrated expression of fire controls is studied through analysis of discrete fire events compiled from historical data or simulations. Landscape burn probabilities are estimated from computationally complex simulation models or predictive statistical models. Unfortunately, because burn probabilities are investigated through the narrow lens of discrete fire events, results are limited to conditions represented within the analysed set of fires and associated mix of static and dynamic fire controls, which may or may not represent possible or likely fire outcomes in the future. In contrast, decoupled metrics of fire controls are generated with direct measurement of the fire control itself in a deductive approach that facilitates broad generalization and ease of estimation across large areas. This approach is well established for mapping spatial variation in weather controls on fuel moisture and fire behaviour, which are estimated over a range of time scales (i.e., daily, annual, decadal), irrespective of fuel conditions.

Fig. 6

Conceptual contribution of the exposure metric to landscape fire risk modelling. a In probabilistic models of fire likelihood, the integrated expression of fire controls is studied through analysis of discrete fire events compiled from historical observations or simulations. Landscape burn probabilities are estimated from simulation or predictive statistical models and are limited to conditions represented by the set of analysed fire events. b Decoupled metrics of fire controls can be used alone or in combination with other relevant fire controls to infer fire likelihood. These metrics are estimated from a deductive approach that facilitates broad generalization and ease of estimation across large areas. The approach is validated by testing for alignment with observed wildfires

Fire weather indices are calculated and mapped across entire countries solely from weather station measurements of temperature, relative humidity, wind speed and precipitation (i.e., Van Wagner 1987). These metrics omit fuel conditions but are well-established as significant predictors of wildfire activity and have made important contributions to the study of fire processes, such as facilitating temporal comparisons instrumental for detecting climate change impacts (e.g., Flannigan et al. 2005). Efforts to develop comparable fuel-based metrics may have been eclipsed by the availability of complex fire spread simulation models, which have the perceived advantage of accounting for spatial context in the assessment of fire-prone locations. Figure 6 illustrates the conceptual process of evaluating landscape fire exposure in relation to multiple independently derived metrics of fire controls, such as fire weather indices, ignition frequencies, topography or fire response. Our results suggest that exposure alone can also provide reliable insight about which landscape locations are most prone to burning, a finding consistent with prior studies (e.g., Krawchuk et al. 2006; Beverly 2017) that suggest vegetation feedbacks strongly regulate fire in our study area.

Future research

In our study area, pre-existing, coarse-scale fuel type data were sufficient for accurately assessing spatial variation in fire exposure in ten of eleven ecological units examined, despite the many limitations of these fuel data. Our fire exposure metric also performed well despite ignoring most of the variables commonly used to assess potential fire behaviour and fire likelihood at the landscape scale, including topography, weather, wind speed and direction, season, and fire regime characteristics typically derived from historical data such as ignition agents, ignition patterns and fire frequency. Further research will be required to assess the individual contribution of exposure and other decoupled fire controls towards overall fire likelihood in an area, for example by using exposure as an input to probabilistic statistical models. Predictive models of fire occurrence could also be used to assess the influence of our exposure metric in relation to other landscape metrics (e.g., Vega-Garcia and Chuvieco 2006). Further study is also needed to explore practical applications of the exposure metric for documenting landscape change over time and for informing fire management decisions such as proactive vegetation management and evacuation planning. While the results of our study are promising, the exposure metric will require further evaluation for use in ecosystems that depart from the fire regime and fire environment characteristics of our study area.