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Seed Viability and Fire-Related Temperature Treatments in Serotinous California Native Hesperocyparis Species

Abstract

Fire-prone serotinous California Hesperocyparis L. (cypress) have been experiencing low seedling recruitment, underscoring our need to better understand these species’ responses to fire. We investigated the specific heating conditions required to break cone serotiny and to promote seed dispersal by focusing on five Hesperocyparis species of interior California: Hesperocyparis nevadensis (Abrams) Bartel, Paiute cypress; H. bakeri (Jeps.) Bartel, Baker cypress (also known as Modoc cypress); H. forbesii Jeps. Bartel, tecate cypress; H. macnabiana (A. Murray bis) Bartel, McNab’s cypress; and H. sargentii (Jeps.) Bartel (Sargent’s cypress). A muffle furnace was used to conduct eight temperature treatments of 250 °C to 700 °C, ranging in duration from 30 seconds to 5 minutes of exposure. The heat-released seeds were tested for viability using a tetrazolium red stain. Logistic regression analysis of seed viability indicated that duration of heating alone was highly significant (P < 0.005) for all species, regardless of temperature, with durations of 1 min or less resulting in the greatest viability. Hesperocyparis forbesii and H. nevadensis were capable of tolerating temperatures as high as 700 °C. Models predicting seed viability reflected interspecific differences, with H. macnabiana and H. sargentii having higher seed viability than H. nevadensis and H. forbesii, which had higher seed viability than H. bakeri. Lab results coupled with field observations following fire suggest that fire can trigger a massive release of seeds, overwhelming the inherently low viability and allowing for greater potential for adequate seedling establishment.

Introduction

Woody plants have developed specific and elaborate reproductive and recruitment adaptations in areas where fire is a consistent ecological process. Cone serotiny, the retention of a canopy seed bank in protective structures for more than one year, is often common in such habitats, along with other traits such as resprouting and flammable foliage (Agee 1993, Bond and Keeley 2005). While prevalent among angiosperms in Australia and elsewhere in the southern hemisphere (Lamont et al. 1991), serotiny is mainly confined to the conifer genera Pinus (pine) and Hesperocyparis (cypress) in North America (Zedler 1977, Mc-Master and Zedler 1981, Barbour 2007). Some evidence implies that the presence of serotiny among other fire-adapted traits indicates a close relationship with stand-replacing fires that occur at intervals long enough for trees to reach reproductive maturity (McMaster and Zedler 1981, Agee 1993, Pausas et al. 2004). The primary advantage of cone serotiny is that seeds are released when conditions, such as growing space or light availability, are favorable for regeneration (Lamont et al. 1991, Keeley and Zedler 1998). For many serotinous species, heat is required for the cones to open and release seeds (Beaufait 1960, Vogl et al. 1977, Bradstock and Myerscough 1981, Zedler 1986, Enright and Lamont 1989, Lamont 1991, Clarke et al. 2010), although the degree and mechanism of serotiny varies by species (Vogl 1973, Harvey et al. 1980), and sometimes by population (McMaster and Zedler 1981, Mallek 2009). The degree and mechanisms of cone serotiny, and linkages between heating regime and seed release, while well documented in angiosperms of Australia, is largely unknown for many North American conifer species, an obvious disadvantage to their restoration and management.

Among species noted for cone serotiny, but for which little information is known, are the Hesperocyparis species of southwest North America (Vogl et al. 1977; Mallek 2009). Californian Hesperocyparis have restricted native ranges (McMillan 1956, Vogl et al. 1977, Zedler 1977) and are usually dependent on fire for regeneration, as reflected by the dominance of serotiny in the genus (Wolf 1948, Bartel 1993). Hesperocyparis species are limited to isolated populations and are often associated with harsh, dry sites subject to extreme temperature fluctuations, and grow on serpentine, volcanic, or granitic substrates at elevations ranging from 300 m to 2100 m (Stuart and Sawyer 2001). Hesperocyparis species are facing a variety of possible threats to their perpetuation, and some populations are experiencing fire regimes and fire behavior altered from historic norms, with some being negatively affected by long-term fire exclusion (K.E. Merriam, USDA Forest Service, Quincy, California, personal communication). Other Hesperocyparis populations are threatened by extirpation from too frequent stand-replacing fires as a result of anthropogenic ignitions (de Gouvenain and Ansary 2006). The many-faceted threats faced by Hesperocyparis populations require a more thorough understanding of the conditions leading to successful seedling recruitment following stand-replacing fires.

Of the ten species native to California, this study examined the five Hesperocyparis species most susceptible to fire due to their location and habitat: Hesperocyparis nevadensis (Paiute cypress), H. bakeri (Baker cypress), H. forbesii (tecate cypress), H. macnabiana (McNab’s cypress), and H. sargentii (Sargent’s cypress). After decades of fire exclusion, some interior California Hesperocyparis species face the paradox of wildfire threatening their perpetuation and, at the same time, fire being necessary to open serotinous cone scales and to prepare receptive seed beds. When high intensity fires occur too frequently, fire-dependent species become susceptible to an “immaturity risk,” by which young trees are killed before reaching reproductive age (Zedler 1977, Keeley and Fotheringham 2000), which is estimated to be between 10 yr and 15 yr in Hesperocyparis (Bartel 1993). Hesperocyparis forbesii populations have been shown to require fire return intervals longer than 40 years in order to develop an adequate canopy seed bank, and are vulnerable to extirpation from fire return intervals that are substantially less than 40 years (Zedler 1995, de Gouvenain and Ansary 2006).

The most northern Hesperocyparis species, H. bakeri and H. macnabiana, face a different challenge of altered stand conditions, possibly due to fire exclusion. Increases in shade-tolerant species and changes in stand density have put some populations of H. bakeri at risk of being out-competed (Keeler-Wolf 2004a). Hesperocyparis bakeri has been experiencing increased interspecific competition and greater stand density in areas that have experienced prolonged fire exclusion. Evidence of poor seedling regeneration and competition from shade-tolerant Abies concolor (Gord. & Glend.) Lindl. ex Hildebr. (white fir) were observed on the Plumas and Lassen national forests by both Wolf (1948) and Stone (1965), and later by Keeler-Wolf (2004a). A long history of fire exclusion has left some Hesperocyparis populations facing a risk of cone senescence before fire can prepare the seedbed, resulting in little or no regeneration when fires do occur (Keeley and Fotheringham 2000). As prescribed fire may be an essential tool in restoring fire regimes in these historically fire-dependent ecosystems, determining the temperature regimes required to break cone serotiny and to allow subsequent seed germination for Hesperocyparis species is necessary.

Experiments with Pinus species (Saracino et al. 1997, Schwilk and Ackerly 2001) and with Hesperocyparis species (Ne’eman et al. 1999, de Gouvenain and Ansary 2006) have shown that traits such as highly flammable foliage, dead branch retention, and cone serotiny are strongly correlated with high-severity fire regimes. But little information exists on the specific environmental conditions necessary for cone opening and regeneration (Vogl et al. 1977, Mallek 2009). Very high temperatures have been shown to reduce the germination ability of Pinus seeds (Torres et al. 2006, Moya et al. 2008), but are required in strongly serotinous species to open cones and release seeds (Vogl 1973, Habrouk et al. 1999, Reyes and Casal 2002). The primary focus of this study was to determine the specific heating conditions required to break cone serotiny of inland California Hesperocyparis species and to promote seed dispersal, while minimizing seed injury. In particular, specific study objectives were to determine: 1) the minimum heat load (i.e., temperature and duration) required for Hesperocyparis cones to break serotiny; 2) the effect of cone heat load on seed viability; and 3) whether individual species respond differently to heat loads. Study results provide a better understanding of how Hesperocyparis regeneration is affected by fire, allowing wildland fire managers to better manage and restore extant Hesperocyparis stands.

Methods

Field Data Collection

We sampled five interior California Hesperocyparis species over a three month period from June to August, 2008. We located the study sites from the northern to southern end of California (Figure 1). Cones were collected from 18 trees at each of five sites, for a total of 90 trees sampled. A branch with at least ten cones was cut from each tree at 2 m above the ground. To avoid moisture loss, live branches were collected rather than individual cones. Cut branches were kept moist with wet paper towels in plastic bags and stored in a cooler containing ice for a maximum of 72 hours, in transit to the lab. Samples were refrigerated at 3 °C to 5 °C until the heat treatments commenced, usually within 48 hours. Cones from the 18 trees (for each species) were systematically mixed together so that each treatment cell had cones from different trees. Cones selected for heat treatments were located near the ends of branches, avoiding those on the tips of branches that were brown, indicating immaturity (first- to second-year cones). Cones that were gray in color with a peduncle (indicating the cones were at least 3 yr to 5 yr old) on each branch were used for the treatments (Figure 2). Cones closer to the tree than the outer 0.5 m to 0.8 m of the branches were avoided as these were usually older than 5 years and invaded by burrowing insects, leading to premature desiccation.

Figure 1
figure1

Range of all five native California Hesperocyparis used in the study. Circles indicate the sampling locations; H. macnabiana and H. sargentii were collected at the same site in Lake County, California, USA.

Figure 2
figure2

Hesperocyparis nevadensis (Paiute cypress) branch showing the typical sequence of cones, 3 years and older (note the gray scale color) that was collected from each tree. Sequoia National Forest, Tulare County, California, USA.

Additionally, we collected seeds from the H. macnabiana collection site in Lake County, California, following the 2008 Walker Fire that occurred in the same population three weeks after live cone collection. The goal was to see if the seed viability from the post-fire plots matched the seed viability measured for any specific heat treatment. The seeds were collected from five ground plots and five canopy plots in August, two months after the fire. Plots were 0.5 m × 0.5 m and at least 150 seeds were collected from each plot. The seeds from canopy plots were obtained by gently tapping branches with open cones over 0.5 m × 0.5 m trays. Seed density was estimated at 600 m−2 to 800 m−2 from the five ground plots. All collected seeds were transported to the laboratory in closed containers and tested for seed viability.

Heat Treatments

A pilot study conducted with H. macnabiana found, through a combination of branch burning and oven treatments, that cones began to open at cone surface temperatures ≥250 °C. The branches were burned under laboratory conditions to measure temperature duration, using insulated iron-constantan (Type K, 2 mm diameter) thermocouples wrapped around the branch and set next to the cones, and connected to a CR1000 datalogger (Campbell Scientific, Logan, Utah, USA). The branches were secured to a metal rod a few centimeters above the source of flaming heat (a fuelbed of the same species’ dry litter and foliage) on a laboratory burn platform beneath a 3 m × 3 m exhaust hood. This technique was later repeated with H. sargentii, H. nevadensis, and H. forbesii, but not with H. bakeri.

Based on the results of the pilot study, heat treatments of 250, 300, 350, 400, 500, 600, 650, and 700 °C were used. The time exposure treatments consisted of 0.5, 1, 2, 3, 4, and 5 minutes. Not all combinations of temperature and time were tested due to the pattern of shorter durations of heat exposure at increased temperatures found in a pilot study conducted before the actual experiment, so there was a total of 36 time × temperature treatments on 900 cones. At the time of treatment, cones were cut from the branches and then randomly selected, using five cones per treatment combination. A control for each species (no heat treatment) was maintained at room temperature on the same starting day as the other treatments and monitored the same length of time as the treated cones (35 days). A muffle furnace (Thermolyne Sybron Corporation, Dubuque, Iowa, USA; Model No. F-A1730) with a temperature range of 0 °C to 1000 °C was used for all of the heat treatments. For each heat treatment, the cones were set in a crucible and placed in the muffle furnace. The heating of the crucible was accounted for by measuring the surface temperature while in the muffle furnace with a thermocouple and adjusting the set temperature.

Seed Viability Tests

The amount of scale opening (mm) following heat treatment each day was measured with a set of calipers, and the number of seeds released was recorded for a minimum of 35 days. A cone was considered open when the scales had opened at least 4 mm because only then could the seeds fit through the opening. Cypress cone scales tend to separate at the same time and in a uniform pattern. All seeds released from cones were tested 60 days later for germination. Lots of 25 seeds for each treatment of each species plus the control were pre-chilled at 3 °C to 5 °C for 21 days on moist filter paper in Petri dishes, and then placed in a germination chamber (Stults Scientific Engineering Corporation, Springfield, Illinois, USA). The seeds were subjected to an alternating temperature regime of 16 hours at 20 °C, and 8 hours at 30 °C each day for at least 30 days, following the guidelines for Hesperocyparis species set forth by the Association of Official Seed Analysts (2008). Germinated seeds were counted each day to quantify total percent germination for each treatment and species.

After conducting two germination trials (50 total seeds tested per treatment), all H. macnabiana and H. sargentii seeds failed to germinate. To get a more complete picture of seed viability in these and the other Hesperocyparis species, live staining was applied to new, untested seeds following the conclusion of germination tests. The seeds were tested with a 1 % tetrazolium red solution at 30 °C to 32 °C, for 12 hr to 18 hr, following the tetrazolium testing procedures outlined by the Association of Official Seed Analysts (2001). The stained seeds were cut and analyzed visually for viability based on the staining extent and the condition of the embryo (Figure 3), with only a completely stained embryo considered viable (Association of Official Seed Analysts 2001).

Figure 3
figure3

Hesperocyparis sargentii (Sargent’s cypress) seeds cut longitudinally, showing the four categories of observation: (a) full stain of embryo; (b) incomplete stain of embryo; (c) unstained embryo; and (d) embryo absent. For all species studied, only (a) was considered viable.

Statistical Analysis

Logistic regression (Hosmer and Lemeshow 2000) was used to assess the effect of the heating duration and temperature on the probability of seed viability following heat treatment, and to determine if these differed between the five species (after Escudero et al. 1999; Nuñez et al. 2003). The temperature and time of exposure of treatments were selected as the predictor variables (main effects terms). The entire model, which included temperature, time, the interaction of the two, and independent terms, was tested along with all reduced (i.e., additive) models. A species effect term (representing the seed viability data of both species combined to test for significant differences) was included for all models that tested for differences between species.

Logistic relationships are expressed as the following model:

$$P = {1 \over {1 + {e^{ - z}}}}$$
(1)

where P is the probability of seed viability and z is a linear function containing the predictor variables included in the model (z = b 0 + b 1 × temperature + b 2 × time + b 3 × temperature × time). The coefficients of the z function were estimated using the maximum likelihood function. The models were selected based on the significance of the variable (using the P-value of the coefficients) and the change in deviance, which is the value of the change in the −2 log likelihood between the model with and without predictor variables (Hosmer and Lemeshow 2000). A deviance value is meaningless unless compared to those of models with predictor variables added in one at a time, and a negative change in the value is considered a better fit. Testing of assumptions and residual diagnostics of the model were conducted using procedures described by Hosmer and Lemeshow (2000). This included assessing whether the variables were dichotomous, the outcomes were statistically independent, the model was correctly specified, and that the categories of viable or not viable were mutually exclusive and collectively exhaustive. Model fit was assessed by the calculation of percent correctly classified predicted values from the models, and plotting the residuals of the deviance values. All statistical analyses were carried out in R, an open source statistical program (R Development Core Team 2009).

Results

All but one of the Hesperocyparis species had similar heat thresholds for breaking cone serotiny. Four of the Hesperocyparis (H. nevadensis, H bakeri, H macnabiana, H sargentii) opened when heated at 500 °C for at least 2 minutes, resulting in substantial release of seed (>50 % of total seed release) (Figures 4 and 5) compared to the control (Table 1). Hesperocyparis forbesii also had a threshold at 500 °C, but only for durations of four minutes and longer (Figure 5b). Even at 600 °C to 700 °C, the proportion of H. forbesii seeds released was low relative to the other species that appeared to be nearing complete release of seeds eight days after treatment, for a greater range of treatment combinations. For example, the cones of H. sargentii and H. macnabiana exposed to 700 °C released nearly 100 % of their seeds after four days (Figure 4). Hesperocyparis bakeri, the most northerly species, released more of its seeds compared to H. forbesii (the most southerly species in California) four days following heat exposure (Figures 4 and 5). Heat treatments increased the chance and rate of cones opening and seeds released compared to the control. Across species, untreated cones did not begin to open until at least 21 days. Even though the control for H. bakeri had the shortest time (21 days) before the cone scales opened at least 1 mm, it was approximately five more days before seeds were released (when cones opened at least 4 mm). In contrast, all H. forbesii cones and most of H. nevadensis failed to open after 40 days (the end of the experiment period).

Figure 4
figure4

The cumulative proportion (compared to the total released at the end of the experiment period) of seeds released at four days following heat treatment for Hesperocyparis bakeri (Baker cypress), H. macnabiana (McNab’s cypress), and H. sargentii (Sargent’s cypress) respectively, showing all temperature and time combination treatments.

Figure 5
figure5

The cumulative proportion (compared to the total released at the end of the experiment period) of seeds released at four days following heat treatment for Hesperocyparis nevadensis (Paiute cypress) and H. forbesii (tecate cypress) respectively, showing all temperature and time combination treatments.

Table 1 Comparison of time (days) until control cones opened, number of cones open, and seed release data for all five species studied.

Germination results revealed three important overall trends related to duration and temperature, and timing of germination: (1) seeds exposed to higher temperatures (400 °C and above) had higher germination rates for shorter exposure periods, and no germination in seeds exposed to heat for more than two minutes; (2) there was a higher percentage of seed germination for all species at the lower temperatures than at the higher temperatures for short exposure times; and (3) the timing of germination of seeds from the northern species was different than those of the southern species. For Hesperocyparis forbesii and H. nevadensis (the southern-most species), germination began to occur on day 7, while for H. sargentii and H. bakeri (more northern species), germination began later, on day 14. Within the first 30 days of the germination trial, the H. forbesii control had the highest germination capacity of 36 %, compared to only 8 % for the H. bakeri control, and no seeds germinated from the other species. Hesperocyparis sargentii had a slow germination response, with a few seeds germinating after 30 days of treatment. Because of very low germination rates for H. macnabiana and H. sargentii, the germination trials were complemented with a seed viability trial using tetrazolium red staining.

Hesperocyparis macnabiana seeds collected within the burned area of the Walker Fire had an average viability of 16.8 % for the ground plots and 12.8 % for the canopy plots, with viability ranges of 12 % to 20 % and 0 % to 28 %, respectively. Seed viability of the control (no heat treatment) for H. macnabiana was 16 %, 20 % for H. bakeri, and 8 % for H. sargentii. The control for H. nevadensis had a seed viability of 12 %, and 24 % for H. forbesii.

The results obtained with the logistic regression models show that all species’ probability of seed viability is negatively affected by increased exposure to heat. Hesperocyparis macnabiana had the greatest seed viability probability (20 %) for low temperature exposures (up to 300 °C), followed by H. forbesii (19 %). For all species, heating time had a highly significant (P < 0.005) effect on the probability of seed viability for all species tested (Table 2). For exposure times longer than two minutes, the probability of seed viability was very low (0 % to 3 %) for H. nevadensis, H. bakeri, and H. forbesii. Hesperocyparis macnabiana and H. sargentii had predicted probabilities of 3 % and 2 %, respectively, but still had some predicted seed viability at five minutes of exposure.

Table 2 Logistic models fitted for all five Hesperocyparis species in the study, along with measures of deviance of the model terms and correct classification (%) of predicted model outputs. The best-fitting models are designated by the associated deviance, in bold. T = Temperature, t = time, model terms in bold are significant using a probability level of 0.05, model terms in italics indicate not significant, deviance values in bold indicate selected models, * = P < 0.05, ** = P < 0.01, *** = P < 0.001, ns = not significant (P > 0.05). Where P-values of model terms have the same level of significance, only one sign is used (i.e., *** for both T and t), for simplicity.

The effect of temperature on probability of seed viability was significant for all species except for H. nevadensis (Table 2). Predicted H. macnabiana seed viability decreased from a maximum of 12 % to 4 % between 250 °C and 400 °C, respectively. Hesperocyparis forbesii, H. nevadensis, and H. sargentii all followed a similar declining pattern in probability of seed viability as temperature increased. Hesperocyparis bakeri was the most sensitive to temperature exposure and displayed a much lower probability of seed viability in general, with a maximum predicted viability of 5 % at 0.5 min and then decreasing to 1 % at 2 min. The model with the interaction of time and temperature was only significant for H. forbesii and H. nevadensis (Table 2).

The results show three important differences amongst the species comparisons. First, there was no significant difference between H. macnabiana and H. sargentii seed viability responses to heat exposure (Table 3). Second, the situation was the same for H. forbesii and H. nevadensis. Hesperocyparis bakeri differed from the other species (Table 3), so the original model (T, t) was used (Table 2). Third, the predicted probability of viability of H. bakeri was low compared to the other four species across all durations and temperatures of exposure (Figure 6).

Figure 6
figure6

Probability of seed viability of the best-fitting combined (comparing one species at a time to another) final models of five serotinous California Hesperocyparis species as a function of heating temperature, for 0.5, 1, and 3 minutes of heating exposure time, respectively.

Table 3 Logistic models fitted for the species interactions of the five Hesperocyparis species in the study, along with measures of deviance of the model terms and correct classification (%) of predicted model outputs. The best-fitting models are designated by the associated deviance in bold. T = Temperature, t = time, S = species term, model terms in bold are significant using a probability level of 0.05, and model terms in italics indicate not significant, deviance values in bold indicate selected model, * = P < 0.05, ** = P < 0.01, *** = P < 0.001, ns = not significant (P > 0.05). Where P-values of model terms have the same level of significance, only one sign is used (i.e., *** for both T and t), for simplicity.

All of the models predicted probabilities of seed viability less than 30 % for all species, as can be seen in Figure 6. The results of the classification tables, in which the percent correctly classified probabilities of the predicted model was compared to the percent of the observations, were all greater than 95 % (Tables 2 and 3). The coefficients of the selected models are also provided in Tables 2 and 3.

Discussion

Our study found that, across Hesperocyparis species, seed germination ability is negatively impacted by prolonged exposure to high temperatures. There appears to be a trade-off between temperature and exposure time for stimulating seed release while simultaneously maintaining viable seed. High proportions of seed were more frequently released at higher temperatures (650 °C to 700 °C) and at greater exposure times, yet for nearly all species, no seed viability was found at these temperatures. While fire intensities (including temperature) vary tremendously within fires (Alexander 1982), these Hesperocyparis species will open their cones and release viable seeds under most of the temperatures tested, although seeds will not be viable under the most extreme temperatures. Similar results in studies found strongly serotinous Banksia shrub species released substantial seed amounts with high heat exposure (Bradstock and Myerscough 1981, Lamont and Barker 1988), and seed viability decreased with high temperature exposure in Pinus banksiana Lamb. (jack pine) (Beaufait 1960).

Hesperocyparis species may be at a competitive disadvantage in re-colonizing a site following severe crown fires with long residence times, as has been observed in stands of H. bakeri (K.E. Merriam, personal communication). Hesperocyparis species seedlings are usually less competitive than other, more shade-tolerant species, so optimal Hesperocyparis seedling establishment occurs in the first year following fire (K.E. Merriam, personal communication). Serotinous Banksia shrubs in Australian heathlands also have the best seedling establishment in the first year following fire (Enright and Lamont 1989). As angiosperms, the Banksia shrubs have adapted to a similar dry climate in shrub lands and rely on serotiny and resprouting for stand re-establishment (Zammit and Westoby 1987, Lamont 1988, Enright and Lamont 1989, Whelan et al. 1998). The coniferous Hesperocyparis species are obligate seeders and therefore must rely exclusively on serotiny in fire-prone ecosystems. Hesperocyparis species’ successful ability to exploit a narrow ecological niche with little competition may also be their greatest weakness in terms of large, landscape-level threats such as altered fire frequencies, increased land development, and changing vegetation composition (K.E. Merriam, personal communication).

Cones were selected from trees in isolated populations, and their patterns of serotiny may differ from other sites, but these broad patterns found suggest that there are differences between the northern and southern species’ cone responses to heat exposure, and the ability of seeds to germinate. Hesperocyparis forbesii cones were more resistant to breaking serotiny, as has been found in previous studies (Garcillan 2010), but were more likely to germinate within one week of placement in the germinators. Hesperocyparis bakeri cone serotiny was easier to break at lower temperatures, but fewer seeds germinated within two weeks. Hesperocyparis bakeri was more heat sensitive than the other four Hesperocyparis species, with more seeds released sooner and with lower seed viability at higher temperatures or longer exposure to heat. Hesperocyparis forbesii was the most heat tolerant species, requiring a much longer time to open and release seeds, and its seed viability was less affected by high temperatures (Figure 6). These trends may reflect different geographic locations, climates (e.g., temperature regime and onset of precipitation), and habitats where these species occur (Table 4). However, since multiple cones were collected from individual trees, there is a possibility that samples may have been pseudoreplicates. Although not previously studied in Hesperocyparis species, variations in serotiny due to the influences of climate and fire regime have been found in studies of serotinous Banksia species in Australia (Cowling and Lamont 1985, Bellairs and Bell 1990).

Table 4 Fire regime requirements for each of the five species studied, by location, north to south. Fire regimes are taken from published literature, heat tolerance is based on original findings of seed viability.

A very low germination rate under laboratory conditions has been consistently found for both H. macnabiana and H. sargentii across different studies (McMillan 1956, Ceccherini et al. 1998) and was confirmed by our study. Our observations in burned H. macnabiana stands and unburned H. sargentii stands suggest that natural germination does occur in high numbers. Field observations made one year following the Walker Fire revealed 12 seedlings m−2 to 20 seedlings m−2 in the same location of the seed release measurements. Other locations of H. macnabiana stands burned within the last ten years reveal heavy local regeneration of this species. Hesperocyparis macnabiana released between 600 seeds m−2 to 800 seeds m−2 after the Walker Fire, suggesting that a mass seed release probably makes up for the low germination ability. The lack of seed germination response in H. macnabiana and H. sargentii also suggests that they may have different germination requirements from the other Hesperocyparis species studied, such as diurnal photoperiod, moisture exposure, or temperature related to their individual climate regime.

Across all Hesperocyparis species in this study, seed viability was negatively affected by greater duration of heating, and to a lesser extent, higher temperatures. During wildland fires, cones are heated for short periods at high temperatures and the seeds are protected from heat exposure by the insulation of the cone, but that protection has been found to lose effectiveness for longer heating durations (Habrouk et al. 1999, Moya et al. 2008) and with decreased cone scale thickness (Linhart 1978). Overall, the requirement of some heat to open cones and release seeds shown for all the species studied here strongly indicates that these species have adapted to fire as a regular occurrence for producing the right conditions for regeneration (Enright and Lamont 1989, Escudero et al. 1999, Habrouk et al. 1999, Goubitz et al. 2003, Nuñez et al. 2003). The fact that there appear to be differential tolerances to heating among the species, and that not all respond the same to various “fire conditions,” suggests that a single fire management approach to all Hesperocyparis species would be detrimental to their perpetuation. As was observed in burned H. bakeri and H. macnabiana stands, seedling regeneration can occur from lightly scorched to completely consumed canopies, regardless of branch or tree death. This implies that not all species need a stand-replacing or even moderate severity surface fire to successfully reproduce. The main limiting factors for regeneration (once the cones are open) appear to be light and moisture. However, the cones must be open first and, as has been shown by our results, some species will open their cones by mechanical removal or desiccation (e.g., removal of branch, burrowing insects, advanced age), but some species like H. forbesii fail to ever open in the absence of substantial heat. This implies that creating canopy gaps around the cypress trees in the absence of fire may only be useful for certain species, such as H. bakeri in which interspecies competition is a significant factor. Factors that must be considered for all species are level of cone serotiny, associated vegetation and fuel, timing of cone maturation, location and extent of populations, local fire history, and historical versus current fire regime.

Previous studies of related serotinous species have investigated variation in the mechanisms of cone serotiny and their ecological and management implications. In previous studies of other cypress species, the heat from a fire is only one of many possible mechanisms for cones to open and spread seed (Lev-Yadun 1995), and although not explicitly measured in our study, some desiccation of older cones was observed and may warrant further study. Unlike the results of our study, Linhart (1978) found a decrease in heat tolerance of seeds of serotinous Pinus species in southern California (versus northern species), and cited seed predation to be a possible driver (along with fire frequency and intensity) of variation in cone serotiny. Similar to the Hesperocyparis species we studied, a lot of variation in cone serotiny occurs in Pinus contorta Douglas ex Loudon and its varieties, and appears to be somewhat related to the elevation and climate of occurrence, historic fire frequency and intensity, type of disturbance (stand-replacing fire versus not) and genetic variation (Lotan 1976, Perry and Lotan 1979, Muir and Lotan 1985, Schoennagel et al. 2003, Pierce and Taylor 2011).

Although a few studies have examined Hesperocyparis species, their life history traits, and regeneration responses to fire (Ne’eman et al. 1999, de Gouvenain and Ansary 2006, Mallek 2009), and others have made observations of botanical characteristics (Jepson 1923; Wolf 1948; Stone 1965; Keeler-Wolf 2004a, 2004b), none have studied the role of heat tolerance directly as was done in this study. As has been shown in previous studies with pines (Despain et al. 1996, Escudero et al. 1999, Habrouk et al. 1999, Reyes and Casal 2002, Nuñez et al. 2003, Torres et al. 2006), Hesperocyparis species in this study responded negatively to high temperatures at longer durations and exhibited similar patterns in seed release, but what is of greater ecological interest and value to management are the differences in individual species’ responses. This is the first study to compare Hesperocyparis species responses to different heat exposures, indicating that further research is needed in examining the role of a species’ regeneration response to contrasting fire behavior, in the context of other competing species. As climate change, increased human activities, and land use practices continue to cumulatively affect fire regimes in landscapes where Hesperocyparis species occur (Westerling et al. 2006, Westerling and Bryant 2008), the need for greater knowledge of these fragmented species mounts.

Literature Cited

  1. Agee, J.K. 1993. Fire ecology of Pacific Northwest forests. Island Press, Washington, D.C., USA.

    Google Scholar 

  2. Alexander, M.E. 1982. Calculating and interpreting forest fire intensities. Canadian Journal of Botany 60: 349–357. doi: 10.1139/b82-048

    Article  Google Scholar 

  3. Association of Official Seed Analysts. 2001. Tetrazolium testing handbook #29, Cupressaceae 2001 update. Association of Official Seed Analysts, Stillwater, Oklahoma, USA.

    Google Scholar 

  4. Association of Official Seed Analysts. 2008. AOSA rules for testing seeds. Association of Official Seed Analysts, Stillwater, Oklahoma, USA.

    Google Scholar 

  5. Barbour, M.G. 2007. Closed-cone pine and cypress forests. Pages 296–312 in: M.G. Barbour, T. Keeler-Wolf, and A.A. Schoenherr, editors. Terrestrial vegetation of California. University of California Press, Berkeley, USA.

    Chapter  Google Scholar 

  6. Bartel, J.A. 1993. Hesperocyparis. Pages 111–114 in: J.H. Hickman, editor. The Jepson manual: higher plants of California. University of California Press, Berkeley, USA.

    Google Scholar 

  7. Beaufait, W.R. 1960. Some effects of high temperatures on the cones and seeds of jack pine. Forest Science 6: 194–199.

    Google Scholar 

  8. Bellairs, S.M., and D.T. Bell. 1990. Canopy-borne seed store in three Western Australian plant communities. Australian Journal of Ecology 15: 299–305. doi: 10.1111/j.1442-9993.1990.tb01034.x

    Article  Google Scholar 

  9. Bond, W.J., and J.E. Keeley. 2005. Fire as a global ‘herbivore’: the ecology and evolution of flammable ecosystems. Trends in Ecology and Evolution 20: 387–394. doi: 10.1016/j.tree.2005.04.025

    Article  Google Scholar 

  10. Bradstock, R.A., and P.J. Myerscough. 1981. Fire effects on seed release and the emergence and establishment of seedlings in Banksia ericifolia L.f. Australian Journal of Botany 29: 521–531. doi: 10.1071/BT9810521

    Article  Google Scholar 

  11. Ceccherini, L., S. Raddi, and H. Andreoli. 1998. The effect of seed stratification on germination of 14 Hesperocyparis species. Seed Science and Technology 26: 159–168.

    Google Scholar 

  12. Clarke, P.J., K.J.E. Knox, and D. Butler. 2010. Fire intensity, serotiny and seed release in 19 woody species: evidence for risk spreading among wind-dispersed and resprouting syndromes. Australian Journal of Botany 58: 629–636.

    Article  Google Scholar 

  13. Cowling, R.M., and B.B. Lamont. 1985. Variation in serotiny of three Banksia species along a climatic gradient. Australian Journal of Ecology 10: 345–350. doi: 10.1111/j.1442-9993.1985.tb00895.x

    Article  Google Scholar 

  14. de Gouvenain, R.H., and A.M. Ansary. 2006. Association between fire return interval and population dynamics in four California populations of tecate cypress (Hesperocyparis forbesii). The Southwestern Naturalist 51: 447–454. doi: 10.1894/0038-4909(2006)51[447:ABFRIA]2.0.CO;2

    Article  Google Scholar 

  15. Despain, D.G., D.L. Clark, and J.J. Reardon. 1996. Simulation of crown fire effects on canopy seed bank in lodgepole pine. International Journal of Wildland Fire 6: 45–49. doi: 10.1071/WF9960045

    Article  Google Scholar 

  16. Enright, N., and B. Lamont. 1989. Fire temperatures and follicle-opening requirements in ten Banksia species. Australian Journal of Ecology 14: 107–113. doi: 10.1111/j.1442-9993.1989.tb01012.x

    Article  Google Scholar 

  17. Escudero, A., M.V. Sanz, J.M. Pita, and F. Pérez-García. 1999. Probability of germination after heat treatment of native Spanish pines. Annals of Forest Science 56: 511–520. doi: 10.1051/forest:19990608

    Article  Google Scholar 

  18. Garcillan, P.P. 2010. Seed release without fire in Callitropsis guadalupensis, a serotinous cypress of a Mediterranean-climate oceanic island. Journal of Arid Environments 74: 512–515. doi: 10.1016/j.jaridenv.2009.09.017

    Article  Google Scholar 

  19. Goubitz, S., M.J.A. Werger, and G. Ne’eman. 2003. Germination response to fire-related factors of seeds from non-serotinous and serotinous cones. Plant Ecology 169: 195–204. doi: 10.1023/A:1026036332277

    Article  Google Scholar 

  20. Habrouk, A., J. Retana, and J.M. Espelta. 1999. Role of heat tolerance and cone protection of seeds in the response of three pine species to wildfires. Plant Ecology 145: 91–99. doi: 10.1023/A:1009851614885

    Article  Google Scholar 

  21. Harvey, H.T., H.S. Shellhammer, and R.E. Stecker. 1980. Giant sequoia ecology. Scientific monograph series 12. US Department of the Interior, National Park Service, Washington, D.C., USA.

    Google Scholar 

  22. Hosmer, D.W., and S. Lemeshow. 2000. Applied logistic regression. John Wiley and Sons, New York, New York, USA. doi: 10.1002/0471722146

    Book  Google Scholar 

  23. Jepson, W.L. 1923. The trees of California. University of California, Berkeley, USA.

    Google Scholar 

  24. Keeler-Wolf, T. 2004a. Mud Lake. Pages 208–211 in: S. Cheng, editor. Forest Service research natural areas in California. USDA Forest Service General Technical Report PSW-GTR-188, Albany, California, USA.

  25. Keeler-Wolf, T. 2004b. Timbered Crater. Pages 285–289 in: S. Cheng, editor. Forest Service research natural areas of California. USDA Forest Service General Technical Report PSW-GTR-188, Albany, California, USA.

  26. Keeley, J.E., and H.J. Fotheringham. 2000. Role of fire in regeneration from seed. Pages 311–330 in: M. Fenner, editor. Seeds: the ecology of regeneration in plant communities. CABI Publishing, New York, New York, USA. doi: 10.1079/9780851994321.0311

    Chapter  Google Scholar 

  27. Keeley, J.E., and P.H. Zedler. 1998. Evolution of life histories in Pinus. Pages 219–247 in: D.M. Richardson, editor. Ecology and biogeography of Pinus. Cambridge University Press, New York, New York, USA..

    Google Scholar 

  28. Lamont, B.B. 1988. Sexual versus vegetative reproduction in Banksia elegans. Botanical Gazette 149: 370–375. doi: 10.1086/337728

    Article  Google Scholar 

  29. Lamont, B.B. 1991. Canopy seed storage and release—what’s in a name? Oikos 60: 266–268. doi: 10.2307/3544876

    Article  Google Scholar 

  30. Lamont, B.B., and M.J. Barker. 1988. Seed bank dynamics of a serotinous, fire-sensitive Banksia species. Australian Journal of Botany 36: 193–203. doi: 10.1071/BT9880193

    Article  Google Scholar 

  31. Lamont, B.B., D.H. Le Maitre, R.M. Cowling, and N.J. Enright. 1991. Seed storage in woody plants. Botanical Review 57: 277–317. doi: 10.1007/BF02858770

    Article  Google Scholar 

  32. Lev-Yadun, S. 1995. Living serotinous cones in Cupressus sempervirens. International Journal of Plant Sciences 156: 50–54. doi: 10.1086/297228

    Article  Google Scholar 

  33. Linhart, Y.B. 1978. Maintenance of variation in cone morphology in California closed-cone pines: the roles of fire, squirrels and seed output. The Southwestern Naturalist 23: 29–40. doi: 10.2307/3669977

    Article  Google Scholar 

  34. Lotan, J. 1976. Cone serotiny—fire relationships in lodgepole pine. Proceedings of the Tall Timbers Fire Ecology Conference 14: 267–278.

    Google Scholar 

  35. Mallek, H.R. 2009. Fire history, stand origins, and the persistence of McNab cypress, northern California, USA. Fire Ecology 5(3): 100–119. doi: 10.4996/fireecology.0503100

    Article  Google Scholar 

  36. McMaster, G.S., and P.H. Zedler. 1981. Delayed seed dispersal in Pinus torreyana (Torrey pine). Oecologia 51: 62–66. doi: 10.1007/BF00344654

    Article  Google Scholar 

  37. McMillan, H. 1956. The edaphic restriction of Hesperocyparis and Pinus in the Coast Ranges of central California. Ecological Monographs 26: 177–212. doi: 10.2307/1948489

    Article  Google Scholar 

  38. Moya, D., A. Saracino, R. Salvatore, R. Lovreglio, J. de Las Heras, and V. Leone. 2008. Anatomic basis and insulation of serotinous cones in Pinus halepensis Mill. Trees 22: 511–519. doi: 10.1007/s00468-008-0211-1

    Article  Google Scholar 

  39. Muir, P.S., and J.E. Lotan. 1985. Disturbance history and serotiny of Pinus contorta in western Montana. Ecology 66: 1658–1668. doi: 10.2307/1938028

    Article  Google Scholar 

  40. Ne’eman, G., H.J. Fotheringham, and J.E. Keeley. 1999. Patch to landscape patterns in post fire recruitment of a serotinous conifer. Plant Ecology 145: 235–242. doi: 10.1023/A:1009869803192

    Article  Google Scholar 

  41. Nuñez, M.R., F. Bravo, and L. Calvo. 2003. Predicting the probability of seed germination in Pinus sylvestris L. and four competitor shrub species after fire. Annals of Forest Science 60: 75–81. doi: 10.1051/forest:2002076

    Article  Google Scholar 

  42. Pausas, J.G., R.A. Bradstock, D.A. Keith, J.E. Keeley, and G.F. Network. 2004. Plant functional traits in relation to fire in crown-fire ecosystems. Ecology 85: 1085–1100. doi: 10.1890/02-4094

    Article  Google Scholar 

  43. Perry, D.A., and J.E. Lotan. 1979. A model of fire selection for serotiny in lodgepole pine. Evolution 33: 958–968. doi: 10.2307/2407658

    Article  Google Scholar 

  44. Pierce, A.D., and A.H. Taylor. 2011. Fire severity and seed source influence lodgepole pine (Pinus contorta var. murrayana) regeneration in the southern Cascades, Lassen Volcanic National Park, California. Landscape Ecology 26: 225–237. doi: 10.1007/s10980-010-9556-0

    Article  Google Scholar 

  45. R Development Core Team. 2009. R: a language and environment for statistical computing, version 2.7.2. R Foundation for Statistical Computing, Vienna, Austria. <http://www.R-project.org>. Accessed 4 February 2010.

    Google Scholar 

  46. Reyes, O., and M. Casal. 2002. Effect of high temperatures on cone opening and on the release and viability of Pinus pinaster and P. radiata seeds in NW Spain. Annals of Forest Science 59: 327–334. doi: 10.1051/forest:2002028

    Article  Google Scholar 

  47. Saracino, A., R. Pacella, V. Leone, and M. Borghetti. 1997. Seed dispersal and changing seed characteristics in Pinus halepensis Mill. after fire. Plant Ecology 130: 13–19. doi: 10.1023/A:1009765129920

    Article  Google Scholar 

  48. Schoennagel, T., M.G. Turner, and W.H. Romme. 2003. The influence of fire interval and serotiny on postfire lodgepole pine density in Yellowstone National Park. Ecology 84: 2967–2978. doi: 10.1890/02-0277

    Article  Google Scholar 

  49. Schwilk, D.W., and D.D. Ackerly. 2001. Flammability and serotiny as strategies: correlated evolution in pines. Oikos 94: 326–336. doi: 10.1034/j.1600-0706.2001.940213.x

    Article  Google Scholar 

  50. Stone, H.O. 1965. Modoc cypress, Hesperocyparis bakeri Jepson does occur in Modoc County. Aliso 6: 77–87.

    Article  Google Scholar 

  51. Stuart, J.D., and J.O. Sawyer. 2001. Trees and shrubs of California. University of California Press, Berkeley, USA.

    Google Scholar 

  52. Torres, O., L. Calvo, and L. Valbuena. 2006. Influence of high temperatures on seed germination of a special Pinus pinaster stand adapted to frequent fires. Plant Ecology 186: 129–136. doi: 10.1007/s11258-006-9117-4

    Article  Google Scholar 

  53. van Wagtendonk, J., and J. Fites-Kaufman. 2006. Sierra Nevada bioregion. Pages 264–294 in: N. Sugihara, J. van Wagtendonk, K. Shaffer, J. Fites-Kaufman, and A. Thode, editors. Fire in California’s ecosystems. University of California Press, Berkeley, USA.

    Chapter  Google Scholar 

  54. Vogl, R.J. 1973. Ecology of knobcone pine in the Santa Ana Mountains, California. Ecological Monographs 43: 125–143. doi: 10.2307/1942191

    Article  Google Scholar 

  55. Vogl, R., K. Armstrong, K. White, and K. Cole. 1977. The closed-cone pines and cypresses. Pages 295–358 in: M.G. Barbour and J. Major, editors. Terrestrial vegetation of California. Wiley-Interscience, New York, New York, USA.

    Google Scholar 

  56. Westerling, A.L., and B.P. Bryant. 2008. Climate change and wildfire in California. Climate Change 87: S231–S249. doi: 10.1007/s10584-007-9363-z

    Article  Google Scholar 

  57. Westerling, A.L., H.G. Hidalgo, D.R. Cayan, and T.W. Swetnam. 2006. Warming and earlier spring increase Western US forest wildfire activity. Science 313: 940–943. doi: 10.1126/science.1128834

    Article  CAS  Google Scholar 

  58. Whelan, R.J., N.H. de Jong, and S. Von der Burg. 1998. Variation in bradyspory and seedling recruitment without fire among populations of Banksias serrata (Proteaceae). Australian Journal of Ecology 23: 121–128. doi: 10.1111/j.1442-9993.1998.tb00710.x

    Article  Google Scholar 

  59. Wolf, H.B. 1948. Taxonomic and distributional status of the New World cypresses. El Aliso 1: 70–91.

    Google Scholar 

  60. Zammit, H.A., and M. Westoby. 1987. Seedling recruitment strategies in obligate-seeding and resprouting Banksia shrubs. Ecology 68: 1984–1992. doi: 10.2307/1939889

    Article  Google Scholar 

  61. Zedler, P.H. 1977. Life history attributes of plants and the fire cycle: a case study in chaparral dominated by Hesperocyparis for besii [in California]. Pages 451–458 in: H.A. Mooney and C.E. Conrad, editors. Proceedings of the symposium on the environmental consequences of fire and fuel management in mediterranean ecosystems. USDA Forest Service General Technical Report WO-3.

  62. Zedler, P.H. 1986. Closed-cone pines of the chaparral. Fremontia 14: 14–17.

    Google Scholar 

  63. Zedler, P.H. 1995. Plant life history and dynamic specialization in the chaparral/coastal sage shrub flora in southern California. Pages 89–115 in: M.T.K. Arroyo, P.H. Zedler, and M.D. Fox, editors. Ecology and biogeography of Mediterranean ecosystems in Chile, California, and Australia. Springer-Verlag, New York, New York, USA. doi: 10.1007/978-1-4612-2490-7_4

    Chapter  Google Scholar 

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Acknowledgements

Special thanks to Dr. Chris Edgar for advice and assistance with the statistical models used in this study. Special thanks to Dr. Bill Bigg and Dr. Pascal Berrill for laboratory assistance. Thanks to Erin Rentz and Fletcher Linton of the USDA Forest Service, and to Joyce Schlachter and Pardee Bardwell of the Bureau of Land Management for collection site access and information. Funding for this project was provided by the USDA McIntire-Stennis Forestry Research Program.

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Milich, K.L., Stuart, J.D., Varner, J.M. et al. Seed Viability and Fire-Related Temperature Treatments in Serotinous California Native Hesperocyparis Species. fire ecol 8, 107–124 (2012). https://doi.org/10.4996/fireecology.0802107

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Keywords

  • cone heating
  • cone serotiny
  • cypress
  • fire temperatures
  • Hesperocyparis
  • seed germination