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Mercury (Hg) stored in vegetation and soils is known to be released to the atmosphere during wildfires, increasing atmospheric stores and altering terrestrial budgets. Increased erosion and transport of sediments is well-documented in burned watersheds, both immediately post-fire and as the watershed recovers; however, understanding post-fire mobilization of soil Hg within burned watersheds remains elusive. The goal of the current study is to better understand the impact of wildfire on soil-bound Hg during the immediate post-fire period as well as during recovery, in order to assess the potential for sediment-driven transport to and within surface waters in burned watersheds. Soils were collected from three southern California watersheds of similar vegetation and soil characteristics that experienced wildfire. Sampling in one of these watersheds was extended for several seasons (1.5 years) in order to investigate temporal changes in soil Hg concentrations. Laboratory analysis included bulk soil total Hg concentrations and total organic carbon of burned and unburned samples. Soils were also fractionated into a subset of grain sizes with analysis of Hg on each fraction. Low Hg concentrations were observed in surface soils immediately post-fire. Accumulation of Hg coincident with moderate vegetative recovery was observed in the burned surface soils 1 year following the fire, and mobilization was also noted during the second winter (rainy) season. Hg concentrations were highest in the fine-grained fraction of unburned soils; however, in the burned soils, the distribution of soil-bound Hg was less influenced by grain size. The accelerated accumulation of Hg observed in the burned soils, along with the elevated risk of erosion, could result in increased delivery of organic- or particulate-bound Hg to surface waters in post-fire systems.
Southern California, with its Mediterranean climate of winter rains and long dry summers, has a fire regime characterized by periodic, and sometimes deadly, wildfires, exacerbated by land use patterns (urban/wild-land encroachment) and a warming climate (Whitlock 2004; Westerling et al. 2006; Keeley and Zedler 2009; CDFFP 2007; Westerling and Bryant 2008). Besides the immediate threat from active wildfires, post-fire watershed conditions raise additional concerns for flooding and debris flows (Cannon et al. 1998, 2001; Cannon and Reneau 2000; Morales et al. 2000; Moody and Martin 2001; Beeson et al. 2001; Gabet 2003; Wondzell and King 2003). Fires are also known to alter stream chemistry (Chorover et al. 1994; Stephens et al. 2005; Meixner et al. 2006; Jung et al. 2009; Mast and Clow 2008), and post-fire storm events have the capacity to carry large sediment loads, mobilizing and transporting heavy metals and other contaminants (Desilets et al. 2007; Rulli and Rosso 2007; Pierson et al. 2008). Of particular concern is the potential movement of mercury (Hg) into downstream water bodies, where conditions may be conducive for the formation of methyl mercury (MeHg), a potent neurotoxin with a strong tendency to bio-magnify within the food chain (Caldwell et al. 2000; Amirbahman et al. 2004; Kelly et al. 2006). However, there is a paucity of data on the impact of wildfire on Hg-soil behavior, which we advocate is critical for the assessment and potential modeling of post-fire Hg transport to surface waters.
Recent studies indicate volatilization of Hg (from vegetation, litter, soils, etc.) during wildfire is an important pathway for the re-emission of atmospherically deposited Hg (Harden et al. 2004; Brunke et al. 2001; Friedli et al. 2001; Friedli et al. 2003a; Friedli et al. 2003b; Sigler et al. 2003; Mailman and Bodaly 2005; Engle et al. 2006; Biswas et al. 2007; Dicosty et al. 2006). Observed losses of Hg, using airborne measurements in smoke plumes or National Atmospheric Deposition Program data, have been used to develop and cross-validate Hg emission models during wildfire (Wiedinmeyer and Friedli 2007; Dicosty et al. 2006). Engle et al. (2006) noted that, although mineral soil was found to contain the largest reservoir of Hg in both the desert and forested sites studied, its contribution to fire-induced Hg emissions was relatively small compared with Hg released from litter and vegetation. The authors also measured higher Hg concentrations in surface ash 1 year following both wildfire and prescribed burns and suggest this was related to sorption of atmospheric Hg over the subsequent year due to Hg's high affinity for carbon in ash (Engle et al. 2006; Olson et al. 2000; Gustin and Ladwig 2004).
Elevated Hg levels have been found in downstream waters of burned watersheds, suggesting that the potential for enhanced mobilization of Hg in post-fire systems persists after the initial threat of fire has passed (Caldwell et al. 2000; Amirbahman et al. 2004; Kelly et al. 2006). Kelly et al. (2006) noted a large, unexpected pulse of both total Hg (THg) and MeHg delivered to a reservoir system in the first post-fire storm event, underscoring that volatilization of Hg to the atmosphere is but one of the ways that fire enhances Hg transport. Fish in a downstream reservoir exhibited elevated MeHg concentrations that were attributed primarily to food web restructuring (Kelly et al. 2006). Caldwell et al. (2000) measured large amounts of Hg mobilized in creek runoff in a freshly burned mixed-conifer forest, as well as a six-fold elevation in the concentration of total Hg and a 30-fold elevation in MeHg concentrations in the sediments of the receiving reservoir near the creek input. The authors hypothesize that particulate organic matter in post-fire runoff not only transported Hg, but lead to downstream sediment conditions conducive to Hg methylation.
Hg transport to terrestrial waters has been associated with suspended sediments and organic matter (Ullrich et al. 2001; Ravichandran 2004). In Hg-enriched sites, such as those contaminated by mining waste or industrial activities, particulate-bound Hg has been shown to control Hg flux in surface waters during storm events (Hurley et al. 1995; Babiarz et al. 1998; Mason and Sullivan 1998; Whyte and Kirchner 2000; Lawson and Mason 2001, Blake et al. 2003). At a Hg-enriched abandoned mine site in Northern California, Whyte and Kirchner (2000) reported that greater than 99.7% of the total Hg transported during storm events was particulate-bound. In a partially urbanized catchment draining to Chesapeake Bay, measured Hg concentrations three to five times higher in storms (over baseflow conditions) were attributed to particulate loading (Mason and Sullivan 1998). Recent work suggests that litterfall and throughfall, as well as the dissolved fraction of organic matter, are important factors in Hg transport in undisturbed watersheds, particularly where snow is the dominant form of precipitation (Bushey et al. 2008). However, suspended sediment concentration remains a controlling factor in Hg flux in disturbed watersheds, including those impacted by fire.
The goal of the current study is to facilitate a better understanding of soil-bound Hg in burned watersheds of semi-arid regions. Particular emphasis is placed on the temporal evolution of soil Hg profiles during the post-fire recovery period and on Hg partitioning within grain-size fractions. We advocate that a better understanding of these processes may ultimately facilitate modeling of sediment-driven Hg transport during post-fire storm events and improve predictions of potential contamination of downstream water bodies.
Mercury concentrations were determined in soils collected from three Southern California watersheds following wildfires in 2005 [Malibu Creek watershed (Topanga Fire)] and 2006 [Arroyo Seco watershed (Pines Fire) and Piru Creek watershed (Day Fire); Table Table1;1; Fig. Fig.1].1]. Preliminary investigations were conducted in the Malibu (Topanga Fire) and Arroyo Seco (Pines Fire) watersheds, and soils were only collected immediately following the wildfires. Analysis of these samples led to more extensive exploration of Piru Creek watershed (Day Fire), where field investigations included both temporal sampling of soil profiles and grain-size analysis. Piru Creek soils were collected immediately following the fire (Fall 2006) and prior to the first storm, as well as seasonally throughout 2007 and the winter of 2008. Stringent sampling protocol (Clean Hands-Dirty Hands) was followed during field collections at all three study areas. Soil samples were collected in new, acid-washed, environmental sampling bottles with Teflon-lined lids using acid-washed plastic shovels. All bottled samples were stored in double plastic bags to avoid contamination and held at 4°C until analysis. Additional soils were collected at each study area for texture classification. Sieve and hydrometer analysis was used to separate material into sand (2 mm–0.05 mm), silt (0.05 mm–0.002 mm), and clay fractions (0–0.002 mm), and soil texture was determined using the USDA NRCS classification system (Soil Survey Division Staff 1993).
Burn severities at each of the study areas were estimated using Moderate Resolution Imaging Spectroradiometer (MODIS) differenced Normalized Burn Ratio (dNBR) and used to aid in the selection of sampling locations (Key and Benson 2006). This index is used by Burned Area Emergency Rehabilitation teams and the California Department of Forestry and Fire Protection to assess landscape-level fire severity. Because of the coarse spatial resolution (1 km) of MODIS imagery, dNBR fire severity assessments were verified with field observations, where burn severity was characterized by percent litter consumed (>50%=low, 100%=moderate) and percent foliage altered (>30%=low, >80%=moderate, and >95%=high; Key and Benson 2006). Water Drop Penetration Tests (WDPT) and infiltration studies were conducted in triplicate at Malibu (Topanga Fire) and Arroyo Seco (Pines Fire) watersheds as well as at Piru Creek (Day Fire) watershed immediately post-fire to assess soil hydrophobicity (DeBano 1981). For the WDPT technique, three drops of water were place on the surface of each sampled layer and allowed to infiltrate the soil. Where all drops infiltrated in <5 s, the soil was classified as wettable, and where all penetration times exceeded 5 s, the soil was classified as water-repellant (Letey 1969). Mini-disk infiltrometers were used to measure soil hydraulic conductivity at the soil surface at all three study areas. Infiltration rates measured using the mini-disk infiltrometers were used to aid in the assessment of soil hydrophobicity.
The Topanga Fire started on September 28, 2005, and was active until October 13, 2005. The fire burned 98 km2 in the Santa Monica Mountains along the border of Los Angeles and Ventura Counties, northwest of the city of Los Angeles (Table (Table1).1). The fire was located primarily in the headwaters of the 282 km2 Malibu Canyon watershed (Fig. (Fig.1).1). Vegetation in the area is primarily chaparral and scrub oak, and the elevations range from 450 to 600 m. Precipitation in the upper Malibu watershed is approximately 450 mm/year. The upper reaches of Malibu Canyon consist of marine sandstones, shales, intrusive tertiary basalts and andesites, and semi-consolidated materials (Ambrose and Orme 2000). Malibu Canyon soils are predominantly coarse and granular in structure, but can vary greatly depending on the parent material (USDA Natural Resource Conservation Service 2007). The dominant texture of soils from the sampling locations was determined to be in the sand-sized fraction.
Soil samples were collected at four burned sites in Malibu Watershed (MB1-4). Unburned soils were not collected at this location. Two sites were sampled in Las Virgenes Canyon on Oct 14, 2005, prior to any precipitation (MB1, MB2), and two sites were sampled in Malibu Canyon on Nov 4, 2005, after the first post-fire storm (MB3, MB4). The Las Virgenes soils were collected at a depth of 2.5 cm; Malibu Canyon soils were sampled at 2.5- and 10-cm depths, with approximately 50 g of soil collected at each depth interval. Three samples were collected at each of the Malibu Canyons sites to account for spatial variability. Soils were analyzed for THg and total organic carbon (TOC).
The Pines Fire occurred in the headwaters of the Arroyo Seco watershed, located on the eastern edge of Los Angeles County in the San Gabriel Mountains (Fig. (Fig.1).1). The fire started September 19, 2006, and was contained by September 23, consuming only ~1 km2 (Table (Table1).1). The San Gabriel Mountains are located on the northeastern edge (windward) of the Los Angeles basin and are known to have high deposition rates of urban pollutants originating from the metropolitan region (Barco et al. 2008). Previous work on the upper Arroyo Seco revealed significant nutrient and other chemical loads contributing to downstream (urban) water bodies (Barco et al. 2008). We hypothesize that fire in these urban-fringe watersheds may exacerbate existing water quality problems and increase downstream chemical loads (US EPA 2007). The upper Arroyo Seco watershed, where the Pines Fire occurred, is approximately 42 km2 and has elevations ranging from 426 to 1,820 m above sea level. Due to its elevation, the Arroyo Seco experiences relatively high precipitation (840 mm/year) compared with the Los Angeles basin (375 mm/year). Vegetation in the upper Arroyo Seco, and at the study sites, is primarily chaparral, with coniferous forests in limited regions of the uppermost part of the watershed. Soils are poorly developed and are underlain by mainly igneous rock including granite, tonalite, gneiss, granodiorite, and to a lesser extent, siliceous metasedimentary rocks, and alluvial deposits (Department of Conservation of California 1998). The soil texture at the sampling locations were determined to be sandy loam and gravelly sandy loam.
Soil samples were collected at four burned sites (ASB1-4) and one unburned site (ASUB1) within the Arroyo Seco watershed during October of 2006, prior to the first post-fire storm. All burned soil sites were collected within 500 m of each other; primary vegetation (prior to burning) was chaparral. Site descriptions are as follows: ASB1and ASB2 were both collected from moderate severity burn areas. ASB3 and ASB4 were collected from areas of low to moderate burn severity. Pre-fire vegetation density was moderate at ASB1 and ASB4, while ASB2, ASB3, and ASUB1 (collected on a nearby hillside) were characterized by dense patches of chaparral. At each site, debris (twigs and large pieces of litter or charred wood) was removed; steep-sided pits were dug, and soils were collected from 0–13-cm depths at 2.5-cm intervals, with approximately 50 g of soil collected at each depth interval. THg and TOC analyses were performed on soils collected from each depth interval.
The Day Fire, which started on September 4, 2006, and was contained by October 13, 2006, burned for over a month and consumed 660 km2 (Table (Table1).1). The burned region is approximately 70 miles north of the city Los Angeles and is almost entirely within National Forest lands (Los Padres and Los Angeles) in the Transverse Mountain Range (Fig. (Fig.1).1). Approximately 50% of the 512 km2 Piru Creek watershed was burned during the Day Fire, with Piru Creek serving as the northern fire boundary. Piru Creek watershed feeds into Pyramid Reservoir, a storage system for imported water from the California State Water Project, which provides drinking water for the Los Angeles metropolitan region. Mean annual precipitation in the region is approximately 480 mm/year. Chaparral is the dominant vegetation, but the watershed's high relief (elevations ranging from 792 to 2,690 m) and Mediterranean climate allow for a wide range of vegetation to exist (Scott et al. 1968). The geology is characterized by pre-Cretaceous igneous and metamorphic basement rock, overlain by thick sedimentary sequences of Eocene marine sandstones and conglomerates with interbedded shales (Scott et al. 1968). Soils are generally shallow and of coarse texture (Scott et al. 1968). The soil texture at sampling locations was determined to be sandy loam.
Soil samples were collected from a network of burned and unburned locations within the Piru Creek watershed on a seasonal basis (Table (Table2).2). This watershed is primarily composed of National Forest lands with very limited access by road; therefore, sampling was conducted in the eastern portion of the watershed, corresponding to the location of the California Department of Water Resources stream gage (Fig. (Fig.1,1, insert). The primary vegetation at all of the burned sites was chaparral (prior to burning), and vegetation density was similar at each site. At the unburned sites, chaparral was the dominant vegetation type, but sage scrub and juniper were also present. Limited access only allowed for initial soil collection from two sites (PCB1, PCB2) on November 17, 2006 (F06), prior to the first storm. Over the subsequent 2006–2007 rainy season (February/March, W07), soil samples were collected from four additional burned sites (PCB3-6) and two unburned sites along Piru Creek (PCUB1, PCUB2). Soil sites were revisited during the summer (June/July) of 2007 (S07) and again in the fall (November) of 2007 (F07), 1 year following the initial sampling date (Table (Table2).2). Soils were sampled again at the end of the 2007–2008 winter rainy season (February/March; W08; Fig. Fig.2).2). When revisiting the sampling sites, soils were collected <0.50 m from the original location. Site homogeneity was verified on the W08 sampling dates by collecting and analyzing triplicate depth profiles at the vertices of a 1 m unilateral triangle (three sites total). Because of the minimal rainfall (~130 mm) and little change in surface conditions in the winter of 2007, soils collected during the fall of 2006 and winter of 2007 were grouped together for subsequent comparisons and are referred to henceforth as F06/W07 (Table (Table2).2). For each site, surface debris was removed; steep-sided pits were dug, and soils were collected from 0–13 cm depths at 2.5-cm intervals, with approximately 50 g of soil collected at each depth interval. Samples were collected at each depth interval for THg and TOC analysis as well as for grain-size fractionation and related THg analysis.
Soil total Hg was measured by dual-stage gold amalgamation/cold vapor atomic fluorescence spectrometry, in accordance with EPA Method 7473, using a Milestone Direct Mercury Analyzer (DMA-80) (US EPA 2002a). The regression coefficient of the daily calibration curves consistently exceeded 0.99 and recovery of standard reference material estuarine sediment (IAEA 405) was consistently within 20% of the established value. Soil sample aliquots of ~500 mg were measured in triplicate or additionally until the relative standard deviation (ratio between standard deviation and mean) was below 0.30. The mean of the triplicate measurements (nanogram Hg per gram) is reported as well as the standard deviation (±nanogram per gram) for all samples.
TOC was determined by loss on ignition (LOI) and derived as a percentage of dry weight. Approximately 1 g of soil was weighed into a pre-burned crucible. The dry weight of the soil was recorded after 12 h in a 105°C oven. The sample was then heated in a 550°C furnace for 1 h, cooled, and reweighed to determine TOC (percent organics).
Soil samples from the Piru Creek watershed (2006 Day Fire) were also size-fractionated at each depth interval prior to THg analysis. Typically, grain-size fractions at the clay/silt break or at the fine/very fine sand break have shown the highest correlations to trace metal concentrations and have been used to normalize data sets from different sampling locations (Horowitz and Erlick 1987; Loring 1991). However, it has also been shown that, in sandy soils lacking sufficient organic material, Hg preferentially sorbs to the coarse mineral soil (Biester et al. 2002). In the current study, soil was fractionated into gravel (>2 mm), coarse sand (0.50-2 mm), medium sand (0.25-0.5 mm), and fine sand (<0.25 mm) according to the USDA NRCS grain-size classification scheme (USDA Natural Resource Conservation Service 1993). Separation of grain sizes less than 0.25 mm was not undertaken for Hg analysis due to risk of sample contamination. Silt and clay were included with the fine sand; this aggregated soil fraction was termed “fines.” All soil samples were weighed, covered, and air-dried for a 10-day period. Any large clumps of soils were then crushed using acid-washed utensils. The soil was placed in an acid-washed, polypropylene micro-sieve set and shaken for 10 min at 140 rpm using a mechanical shaker. The sieved soil fraction was transferred to a pre-tared acid-washed environmental sampling bottle and reweighed. The total Hg content of the coarse sand, medium sand, and fines fractions (and composite sample) was measured to determine the distribution of Hg on varying particle sizes for each depth interval. A bulk sample (at each depth interval and integrated over all sampling depths) was also processed in a similar manner and measured for total Hg.
The USGS field leach test (Hageman and Briggs 2000) was used to analyze Hg leaching on soils collected from two of the Day Fire sites within Piru Creek watershed, one unburned (PCUB2) and one burned (PCB6). Three grams of soil were used due to sample quantity limitations. Representative samples of burned and unburned soils were sieved into two groups: fines (<0.25 mm) and composite (<2 mm), resulting in four groups (unburned fines/composite and burned fines/composite). Of the soil material that passed through the sieves (0.25 mm, 2 mm), portions were set aside for measurement of THg (following EPA method 7473 described above) and TOC by LOI (section 3.2) (US EPA 2002a). The 3 g of soil was weighed into an acid-washed Teflon bottle, to which 60 ml of the reagent water (18 MΩ) was added. The mixture was shaken vigorously for 2 h in a “wrist agitator” and subsequently filtered (0.45um pore size) using an acid-washed syringe. For each of the four groups, duplicate experiments were performed. In order to determine initial concentration of Hg in the soil samples, all four groups were analyzed using the Milestone Direct Mercury Analyzer (DMA-80; section 3.1).
Total Hg analysis was performed on the filtered solution using the Total Hg system by Brooks Rand in accordance with EPA Method 1631, Revision E (US EPA 2002b). This method allows for the determination of Hg at a minimum level of 0.5 ng Hg/L. A sample aliquot was transferred to Teflon-coated bottles, reduced with stannous chloride (SnCl2) to convert Hg(II) to volatile Hg(0), and purged with Argon, allowing the volatile Hg(0) to be transported to gold-coated sand traps. The gold-coated sand traps were then heated for 3 min to 450–500°C to allow desorption of Hg. Argon gas passed through the trap at a flow rate of 30 ml/min to transport the Hg(II) to the cold vapor fluorescence spectrometer, where an absorbance peak was recorded. All samples were measured in triplicate, and the regression coefficient (R2) for daily calibration curves consistently exceeded 0.99. Percent soil leaching was calculated using the following formula:
where Hg is total mercury measured in the leachate (liquid, <0.45-um fraction) and soil; 60 ml is the amount of reagent water added, and 3 g is the amount of soil analyzed.
Analysis of variance was used to compare differences in Hg concentrations and TOC between groups (study areas, seasonal sampling periods, and grain sizes). The analysis was performed using the anova1 function of the Matlab computing program (Mathworks Inc. 2005), with F-tests and p values used as a guide to determine significance at the 5% level.
Due to differences in the sampling regimes between the three burn areas, the regional comparison was limited to soils collected immediately post-fire and to the mean Hg concentrations and organic content of these soils. Bulk soil total Hg (hereafter noted as Hg) concentrations for burned soils at the Malibu Creek watershed (2005 Topanga Fire, MB1-4), averaged over both the 2.5- and 10-cm depth intervals (n=14) ranged from 1 to 37 ng Hg/g, with an average concentration of 17 ng Hg/g (±12 ng/g; Fig. Fig.3).3). Average organic content of the samples was measured 9.4% TOC (±4.4%; Fig. Fig.33).
Bulk soil Hg concentrations for burned soil sites in the Arroyo Seco watershed (2006 Pines Fire, ASB1-4), averaged over the entire 15.0-cm depth profile, ranged from 14 to 349 ng Hg/g, with an average concentration of 134 ng Hg/g (±109 ng Hg/g, n=24), and average organic content of 10.2% TOC (±6.9%, n=24; Fig. Fig.3).3). The unburned soil site (ASUB1) exhibited lower average Hg concentrations with a value of 92 ng Hg/g (±46 ng Hg/g, n=6), ranging from 51 to 176 ng Hg/g. Average organic content in the unburned soils was measured at 17.2% TOC (±14.3%, n=6).
Bulk soil Hg concentrations of the burned soils of Piru Creek Watershed (2006 Day Fire, PCB1-6, F06/W07 sampling period), averaged over the entire 15.0 cm depth profile, ranged from 2 to 44 ng Hg/g, with an average of 18.5 ng Hg/g (±12.9 ng Hg/g, n=25), and low organic content was exhibited in the burned soils of Piru Creek (4.9% TOC; ±2.4%, n=25; Fig. Fig.3).3). In the unburned Piru Creek soils, Hg concentrations ranged from 4 to 67 ng Hg/g, with an average of 19.0 ng Hg/g (±19.8 ng Hg/g, n=12). Very low organic content was measured in the unburned soils in Piru Creek (2.7% TOC; ±1.3%, n=12) soils in comparison to the unburned soils. Our results appear counterintuitive; however, a metadata analysis made by Johnson and Curtis (2001) found increases in soil organic matter in soils affected by wildfire, attributed to the accumulation of charcoal and hydrophic organic matter resistant to chemical and biological degradation. Additionally, due to the size and proximity of the Day Fire, the unburned soils were collected either across the creek or ~2 km upstream, of the burned sites, and it is possible that site heterogeneity contributed to the lower TOC observed in the unburned sites of Piru Creek Watershed.
Mercury levels varied greatly between the three study areas. Proximity to anthropogenic contaminants (L.A. Basin) appears to have an impact on observed soil Hg concentrations, which are significantly (p<0.05) higher in the Arroyo Seco soils than in the other two sites. Both the Malibu and Piru sites (which show similar Hg levels) are located north of the urban/metropolitan center, and regional winds carry urban pollutants inland and away from these regions. These sites exhibit Hg concentrations that are consistent with previously published values in natural, semi-arid systems, such as a Nevada desert wildfire site with measured values of 47.4 ng/g (±26.8 ng Hg/g) and 49.4 ng Hg/g (±11.3 ng Hg/g) of Hg in unburned and burned soils, respectively (Engle et al. 2006). The Arroyo Seco, on the other hand, exhibited Hg concentrations that are more comparable to Hg measured in more humic soils, such as peat bogs in northwestern Ontario where Mailman and Bodalay (2005) measured Hg concentrations of 162 ng/g (±132 ng Hg/g) or even contaminated areas such as those reported by Palmieri et al. (2006), where soil Hg concentrations ranged from 90 to 1230 ng Hg/g at a site draining an abandoned cinnabar (HgS) mine. The Arroyo Seco experienced a much smaller, more confined fire in comparison to Malibu Creek and Piru Creek Watersheds, it is possible that lower loss rates contributed to the higher Hg concentrations observed in the burned soils at this site. The upper Arroyo Seco also receives more rain than the other study areas due to topography and related orographic effects, which may also impact vegetation density. However, similar burn severities were observed in all three study locations. In addition, TOC measurements from the sampled Arroyo Seco sites were in the same range as those observed in the Malibu sites (both were significantly higher than the Piru Creek soil TOC; p<0.05; Fig. Fig.3).3). Hence, we hypothesize that the primary factor effecting elevated soil Hg concentrations is the location/proximity to anthropogenic (urban) sources.
Depth profiles were collected at both the Arroyo Seco (Pines fire) and Piru Creek (Day fire) watersheds. All of the Arroyo Seco profiles and two of the Piru Creek profiles (PCB1 and PCB2) were collected prior to any post-fire rainfall; the remaining Piru Creek profiles were collected after the 2007 rainy season had begun. However, the combination of the watershed's antecedent conditions (dry), the extremely low rainfall totals during the first wet season (ash and charred soil were observed at the burned soil surface) and the similar behavior of these profiles to that observed in the pre-storm samples led to their inclusion in the analysis.
Of the nine burned soil profiles collected in the first season after the fire, eight profiles exhibited lower Hg concentrations at the soil surface (0.0–2.5 cm) than at the next depth interval (2.5–5.0 cm), with the only exception being Day Fire site PCB1 (Fig. (Fig.4).4). The PCB1 site was estimated to have been burned with light severity (using dNBR and field observations) and was also located next to a trail (subject to disturbance). The remaining sites in both study areas were burned with moderate severity (estimated using dNBR and verified by field observations). In contrast to the burned soil profiles, the three unburned soil profiles (Arroyo Seco site AS-UB and Day Fire sites PCUB1 and PCUB2) exhibited the highest Hg concentrations at the soil surface (Fig. (Fig.4).4). The observed low Hg concentrations at the soil surface following wildfire is consistent with other studies of Hg in burned soils and was observed in both the Hg-enriched soils of the Arroyo Seco and the soils of Piru Creek watershed (Mailman and Bodaly 2005; Engle et al. 2006).
Several of the freshly burned depth profiles, from both the Piru Creek and Arroyo Seco locations, exhibited the highest Hg concentrations and TOC measurements between depths of 2.5 and 7.5 cm (Fig. (Fig.4).4). Volatilization of organic matter during fire can move these compounds from the soil surface (in vegetation and litter) to the subsurface where they condense, coating mineral particles and forming a hydrophobic horizon (DeBano 1981; Johnson and Curtis 2001; González-Pérez et al. 2004). Wildfires also affect the chemical properties of soil organic matter and can lead to the formation of pyromorphic humus, which has been shown to change to promote the fixing of polyvalent metals (Giovanni and Lucchesi 1983; Giovanni et al. 1987). Field measurements of WDPT revealed hydrophobicity in all of the burned Arroyo Seco soils at the 2.5–5.0 and 5.0–7.5-cm depth intervals. In the Piru Creek soils, WDPT at the moderate burn severity site sampled prior to the first storm, as well as at one of the burned sites sampled following the winter 2007 storm, also indicated soil hydrophobicity in the 2.5–7.5 cm range.
In general, the low surface Hg levels in first post-fire (F06/W07) Piru Creek sampled sites were accompanied by similar behavior in the corresponding soil organic matter (Fig. (Fig.5),5), supporting previously reported studies of volatilization of surface Hg during the fire. As mentioned above, PCB1 did not exhibit lower Hg concentrations when compared with the 2.5–5.0-cm depth interval, and its light burn severity is evidenced in the corresponding high organic matter levels in the surface soil of this site (Fig. (Fig.5).5). The two unburned sites (PCUB1 and PCUB2) exhibited significantly different behavior than the burned sites (and from each other) with respect to surface Hg and organic matter levels during the W07 sampling period (p<0.05). Site PCUB1 exhibited the highest surface Hg concentrations (67.4 ng Hg/g (±28.4 ng Hg/g)) of all of the Piru Creek sites on the initial sampling date, yet low levels of surface organic matter were observed (1.7% SOM). Other studies have observed increased Hg concentrations in throughfall in areas impacted by wildfire, and we hypothesize that the location of the PCUB1 site may have been subject to enhanced deposition of particulate Hg during the Day Fire (Witt et al. 2009). This site was located beneath chaparral and juniper canopy, and the higher surface Hg concentrations (and low surface TOC) may reflect Hg contribution in the throughfall during the winter 2007 storm.
In order to quantify seasonal changes in soil Hg concentrations and TOC measurements, while accounting for spatial variability between sampling locations, we compared the percent change to determine if there was a significant difference in these constituents between sampling events. Over the subsequent dry seasons (S07 and F07), the average surface Hg concentration of the burned soils increased by 417% (±72%) from the initial sampling date, with the mean Hg of the dry season burned soil surface significantly higher than the initial measurements (p<0.05). This is exemplified in the surface Hg concentrations of the two moderately burned sites for which we had complete temporal sampling (PCB2, PCB4; Fig. Fig.5).5). By the F07 sampling date, the surface soils of PCB2 and PCB4 showed Hg concentrations 50–70 ng/g higher than those measured 1 year previously (Fig. (Fig.5).5). In the case of PCB4, increased Hg values were accompanied by increased TOC over the summer and fall of 2007; the higher Hg concentrations and TOC at this site may be related to vegetation recovery following the fire. The slight increase in organic matter observed at PCB2 is not sufficient to explain the high Hg concentrations observed at the soil surface and throughout the depth profile on the F07 sampling date. The surface soils at these sites were charred, and we hypothesize that the burned soils in the Piru watershed have been chemically altered, with the pyromorphic humus acting as an activated carbon to more efficiently sequester and retain Hg, contributing to higher observed Hg concentrations in the first year following the fire (Giovanni and Lucchesi 1983; Giovanni et al. 1987; González-Pérez et al. 2004). The light burn severity site (PCB1) also exhibited higher organic matter accompanied by higher Hg concentrations in the surface soils in the dry season following the fire (S07, F07; Fig. Fig.55).
Site PCUB1 appears to stabilize by the S07 and F07 sampling dates; the high surface Hg concentrations observed during the initial sampling (F06/W07) were not observed again. Little change was observed in both the Hg concentration and TOC profiles at PCUB1 over the dry season (Fig. (Fig.6).6). Similar TOC and Hg concentration profiles (low) were observed at PCUB2. Of note is that neither unburned site experienced the sharp increase in Hg concentration that was observed in the moderately burned soil surfaces (PCB2 and PCB4) over the post-fire period, nor the increased soil Hg concentrations throughout the depth profile as observed in sites PCB1 and PCB2.
Compared with the first winter season rainfall (130 mm), precipitation during the winter of 2007–2008 (370 mm) was closer to normal (480 mm/year). Given the low rainfall totals, little soil erosion was noted in the first winter season. However, on the W08 sampling date, considerable surface erosion was observed at the field sites, including sheet-flow, rill and gully erosion, and collapsed banks. Additionally, the winter rains of 2008 initiated vegetation re-growth in the Piru Creek Watershed. Moderate vegetative recovery was observed on the W08 sampling date and is reflected in the increased surface TOC measurements in burned soils on this sampling date. Most sites (burned and unburned) exhibited lower Hg concentrations at the surface during the winter of 2008 in comparison to the previous dry seasons (Fig. (Fig.5).5). A 16% (±54%) decrease was observed in the mean surface Hg concentration of the burned sites from the previous season, and a 24% (±6%) decrease was observed in the unburned soils. This was a significant change for the burned soil sites which had previously shown a gain in Hg over the dry seasons (p<0.05). We attribute the low surface Hg concentrations observed at most sites during the W08 sampling period to soil flushing and enhanced erosion at the disturbed (burned) sites and hypothesize that while TOC increased as the pre-fire vegetation began to return, the Hg that had accumulated in the surface soils was generally flushed or carried off with eroded sediment. The enhanced erosion observed following the winter 2008 may also have resulted in a slight shift in some of the vertical profiles.
A comparison of the seasonal Hg concentrations and organic matter levels of the burned and unburned surface soils profiles (all burned soil sites PCB1–PCB6 and unburned sites PCUB1 & PCUB2, surface composite samples, 0.0–2.5 and 2.5–5.0-cm depth intervals; Fig. Fig.7).7). Recovery of vegetation following the wildfire is reflected in the steady increase in organic matter in surface soils over the subsequent seasons. Soil Hg concentrations were initially low on the W07 sampling date and increased over the following dry season sampling period (S07, F07), reflecting the observed TOC increase (as evidenced in the burned site PCB4). Increasing soil Hg concentrations that were not accompanied by increased TOC where also observed (PCB2), indicating possible chemical changes in the soil organic matter. The drop in the mean Hg concentration in the burned soils from W08 was not accompanied by lower TOC values. In fact, the highest observed TOC values were from W08 sampling period, supporting our hypothesis that the lower levels of Hg were most likely due to transport away from the study sites during the winter storms of 2008. For the unburned soil sites (PCUB1 & PCUB2), little change was observed seasonally in the surface organic content. The high initial Hg (W07) concentrations at PCUB1 were not reflected in the TOC values. However, these Hg concentrations dropped by the following season and, like the TOC values, remained relatively constant throughout the following year.
For the burned soils of Piru Creek watershed (all soil samples, integrated over the entire depth profile) 41.94% (±19.75%), 18.88% (±4.68%), and 39.19% (±19.90%) of the soil was classified as fine, medium, and coarse grain-size fractions, respectively (n=76; Fig. Fig.8).8). Significantly higher concentrations of Hg were observed in the fine and medium grain-size fractions than observed in the coarse fraction (p<0.05; Fig. Fig.8).8). Overall Hg distribution in the burned soils included 37.19% (±5.54%) in the fines, 35.43 % (±4.68%) in the medium fraction, and 27.38% (±5.51%) in the coarse grain-size fraction (n=76). Significantly lower Hg concentrations were observed in the coarse grain-size fraction than in the medium and fine-grained burned soils of Piru Creek (p<0.05).
The grain-size distribution in the unburned soils (all soil samples, integrated over the entire depth profile) was similar to that observed in the burned soils with 40.92% (±9.49%), 26.26 % (±9.42%), and 32.82% (±9.93%) of the soil measured as fine, medium, and coarse grain-size fractions, respectively (n=35). Hg distribution in the unburned soils included 53.70% (±13.92%), 29.47% (±9.71%), and 16.83% (±7.68%) in the fine, medium, and coarse grain size fractions, respectively (n=35). Hg appears to be preferentially bound to the fines in the unburned soils of Piru Creek, with Hg concentrations decreasing as the grain size increased (Fig. (Fig.8).8). Hg concentrations were significantly different in each of the fractions (p<0.05).
Others have observed a trend towards coarser soil texture following fire, attributed to heat-induced aggregation of silt and clay particles as well as the introduction of particulate charcoal fractions from litter combustion (González-Pérez et al. 2004). The variability of the Hg distribution within the different grain-size fractions between the burned and unburned soils of Piru Creek is likely a function of multiple factors, including site characteristics (such as native geology, slope, land cover, etc.) as well as fire-induced changes to soil aggregates and soil organic matter. Additional laboratory experiments on Hg binding in pre- and post-fire samples are needed to better clarify the effects of fire on Hg distribution within soil fractions.
Similar to previous research, leaching of soil Hg was minimal (Grigal 2002). Laboratory leach tests showed this to be the case in both the burned and unburned samples. In both cases, more Hg was leached from the bulk sample (<2 mm) than from the fine grain-size fraction (<0.25 mm). In the burned bulk samples, 23.25 ng Hg/g (±1.49) soil was measured in the soil and 0.48 ng Hg/g (±.0.12) soil was detected in the equivalent leachate, hence 2.07%(±0.34%) Hg leached from the burned bulk sample (Table (Table3).3). In the fines, 36.49 ng Hg/g (±3.82) was measured in the soil and 0.21 ng Hg/g (±0.08) soil measured in the equivalent leachate, resulting in only 0.58% (±0.07%) Hg leached from the fines in the burned samples (Table (Table3).3). The unburned bulk samples contained 4.25 ng Hg/g (±0.48) soil with 0.11 ng Hg/g (±0.01) soil measured in the equivalent leachate. Therefore, 3.07% (±0.70) Hg leached from the bulk sample (Table (Table3).3). In the unburned fines, 11.58 ng Hg/g (±1.35) was measured in the soil with 0.09 ng Hg/g (±0.01) soil observed in the equivalent leachate, hence 0.82% (±0.08%) Hg leached from the fine grain-size fractions of the unburned soil (Table (Table3).3). In general, the composite samples leached more Hg than the fines samples for both burned (274% more Hg leached from composite than fines) and unburned soils (257% more Hg leached from composite). However, these data support that Hg not volatilized in the fire may be in a more recalcitrant form, such as complexed to a more resistant form of organic matter (pyromorphic humus) which developed as a result of the fire, as 41–48% more Hg was leached from the unburned than the burned samples, seen in both the fine and composite samples (González-Pérez et al. 2004).
Results from this work support previous published studies that show a loss of Hg in freshly burned soils (Friedli et al. 2003b; Engle et al. 2006). However, the current study expands upon previous results to include observations of soil Hg as a watershed recovers from fire. To summarize, the freshly burned soils exhibited lowest concentrations of Hg at the soil surface (top 0.0–2.5 cm) in all but one of the nine sampling sites burned to moderate severity. The only burned soil profile that did not exhibit this behavior was subject to low burn severity, highlighting the importance of burn severity on Hg mobilization during wildfires. In the three unburned soils sites, the highest Hg concentrations were observed at the soil surface. This behavior was observed both in the Piru Creek watershed, located in a remote location, where the background Hg levels (2 to 87 ng Hg/g) were characteristic of a natural, semi-arid region, and in the enriched soils of the Arroyo Seco watershed, where Hg concentrations of >300 ng Hg/g were observed.
The impact of fire on organic carbon also plays an important role in soil Hg dynamics. A few of the freshly burned depth profiles exhibited the highest Hg concentrations between depths of 2.5 and 7.5 cm, with the highest TOC and hydrophobicity also measured in this range. Following the initial volatilization of Hg at the soil surface during wildfire, the burned soils experienced an accelerated accumulation of Hg following the fire. In the Piru Creek watershed soils, a four-fold increase in mean surface soil Hg concentrations was observed over the subsequent dry season, corresponding to an increase in the mean surface TOC measurements as well as moderate vegetative recovery. However, the relationship is not straightforward, as one of the burned sites exhibited much higher soil Hg concentrations 1 year after the fire with only a slight increase in organic material. We hypothesize that heat-induced changes in soil organic matter resulting from the fire allowed the charred surface soils to more efficiently complex and retain atmospheric Hg. Additional investigations are needed to better understand Hg sorption in burned soils.
Following the second post-fire rainy season, low surface Hg concentrations were observed in the burned and unburned sites, while the organic content of the burned soils continued to increase as the watershed's vegetation began to return. We attribute the loss of Hg in at the soil surface to soil flushing and enhanced erosion (observed) during the winter storms. These results underscore that the observed accelerated accumulation of Hg in the burned soils, along with elevated potential of erosion, could result in increased delivery of organic- or particulate-bound Hg to surface waters. And, depending upon precipitation patterns, this risk may extend beyond the first post-fire rainy season and persist in the years following the fire.
Our grain-size distribution analysis supports that a range of grain-size fractions (not only the fine fraction) need to be considered in soil Hg analysis (Biester et al. 2002). Hg-soil partitioning with respect to grain size was not as strong in the burned soils as in the unburned soils (where Hg preferentially bound to the finer soils). As the time since burning increases, an evolution towards the transport of more coarse sediments occurs in post-fire storm runoff (Desilets et al. 2007). Our results indicate that this coarser material may also be more likely to contain higher concentrations of soil-bound Hg. Although leaching was minimal in both the burned and unburned soils, the difference in Hg leaching between the fine and more coarsely grained soil fractions indicates that coarsely grained soils must also be considered for their potential to contribute to Hg mobilization in burned watersheds.
The current study provides a unique look at soil–Hg interactions immediately after wildfire as well as several post-fire seasons. The accelerated accumulation of Hg observed in the burned soils of Piru Creek watershed, along with observed differences in Hg-soil partitioning within the grain-size fractions in burned and unburned soils, underscores the need for extended water quality monitoring of post-fire watersheds. We advocate that this is especially critical in areas that are subject to high rates of atmospheric deposition of contaminants or above essential water supply systems. Results from this study also raise important questions regarding the mechanisms controlling Hg binding in burned soils, including the role of translocated organic matter in Hg sequestration and retention and in the grain-size distribution of Hg following fire.
Funding for the current work has been supported by NSF Hydrologic Sciences (SGER EAR #0707162), NSF BES Career Grant (BES #0348783), the University of California Toxics and Substances Research and Teaching Program (UCTSR&TP), the University of California's Leadership Excellence through Advanced Degrees (UC LEADS), the National Institute of Health's Minority Access to Research Careers (MARC), and the NIH/NSF UCLA Center for Academic Research and Excellence (CARE) at UCLA. We thank Chu-Ching Lin, Christina Zabalza, Helen Jung, Alicia Kinoshita, Paul Kirchner, Lauren Tomita, and numerous other volunteers who assisted with field campaigns as well as in sample and laboratory processing. We also thank the anonymous reviewers for their insightful comments and suggestions, which were helpful for improving our manuscript.
Open Access This article is distributed under the terms of the Creative Commons Attribution Noncommercial License which permits any noncommercial use, distribution, and reproduction in any medium, provided the original author(s) and source are credited.
Megan P. Burke, Email: ude.alcu@ekrubagem.
Terri S. Hogue, Phone: +1-310-7944239, Email: ude.alcu.saes@eugoht.