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Chapter IIIMangrove survival, growth, and recruitment in lightning-initiated canopy gaps and closed forest sites in Everglades National Park, Florida USA.
MethodsStudy areaThis study examined the mangroves on the southwest coast of Florida, in Everglades National Park, (25°N - 26°N). This area encompasses approximately 60,000 ha of mangrove forest (Figure 1). These mangroves form a continuous band along the coast, varying in width from 0.1 to 15 km (Smith 1994). Tree height generally declines with distance from the coast (Chen & Twilley 1999). The climate is subtropical with an average maximum temperature above 27 °C. Rainfall has a distinct dry and wet season and varied from 86 to 224 cm over a 10-year period (Duever 1994). Tidal amplitude fluctuated from 10 to 60 cm. Three mangrove species [Rhizophora mangle L. (red mangrove), Laguncularia racemosa (L.) Gaertn. (white mangrove), and Avicennia germinans (L.) Stearn (black mangrove)] are found in this area varying from heterogeneous mixed stands to single species dominated forest. Hurricane disturbance to this region is common, with catastrophic hurricanes occurring approximately every thirty years (Doyle 1997). The 1935 Labor Day Hurricane, Hurricane Donna (1960) and Hurricane Andrew (1992) all strongly impacted the Everglades mangrove region. Additionally, lightning-initiated canopy gaps are common in this forest (Chapter I, Houston and Powell 2003, Smith et al. 1994).
I grouped gaps into two ages: (1) three new gaps that were known to have been initiated by lighting between July to September of 2002; and (2) growing gaps, approximately seven to 15 yrs old, generally with a very dense sapling layer. These categories correspond to the following stages within Duke's (2000) small gap mangrove conceptual model: gap initiation combined with gap opening and gap filling, respectively. The growing gap category was assigned based on a subset of gaps of known approximate age (pers. obs. K. Whelan). To compare the community attributes of the lightning-initiated gaps to the surrounding intact forest, I established three intact forest sites. Each of the three groups were comprised of one new gap, one growing gap and one intact forest location (Table 1). At the group location, all gaps of the time series were within 300 m of each other. In this paper, forest stage includes new, growing gaps and intact forest sites whereas the phrase gap phase only refers to comparisons between new and growing gaps.
Additionally, at each gap site the gap size (expanded gap size sensu Runkle 1982), canopy openness (determined by hemispherical photography), distance to river and rivulet and canopy height (mean of six dominant stems) were determined (Table 1). A circular plot (radius eight-m) was established in the center of each gap (site). The plot size was chosen to confine sampling within the canopy gap area. I used the size class definition of Koch (1987) and Chen and Twilley (1998) to ensure comparability of this work with previous studies in this forest. Propagules were not established or rooted in the substrate (i.e. still in a dispersal phase). Seedlings were defined as all individuals attached to the substrate and < 1.4 m in height. Saplings were defined as all stems > 1.4 m and < 4 cm in diameter at breast height (dbh). Adults were defined as all stems greater than 1.4 m in height and Seedlings were tagged and total stem length (soil surface to the dominant meristem) was measured. For R. mangle seedling, the stem length was measured from the top of the propagule scar to the bottom of the leaf sheath of the main meristem. Seedling elongation rates (E-Rate, mm/d) were calculated as (sensu Koch 1997): E-Rate (mm d-1) = (Stem length (t1) - Stem length (t0)) / ((t1) - (t0)) Seedling stem growth (cm yr-1) was E-Rate * 365 days. Sapling and adult tree growth was determined by two successive measurements of dbh. I used the species-specific allometric formulas of Smith and Whelan (in review) to convert from dbh to living biomass. Growth was determined by converting dbh to biomass and determining the relative growth rate (sensu Evens 1977) as: Relative Growth Rate (RGR) = Log (Biomass2) - Log (Biomass1) expressed on an annual basis. Specific per capita recruitment (R) and mortality (M) rates for the sample period were calculated using the following equations (sensu Padilla et al. 2004): R t+1 = Ln{[(Nt + NRt+1)/Nt]/ where R t+1 is the specific recruitment rate annualized, and M t+1 is the specific mortality rate annualized, Nt is the total population at initial survey, NRt+1 is the number of new recruits at the second survey; Dt+1 is the number of dead stems at the second survey; Data analysisAbundance within the propagule class (count data) was For saplings and adult trees the initial dbh, change in dbh, annual change in biomass and relative growth rates were log10 (x+0.5) transformed to increase normality and meet homogeneity of variance requirements for the two-way ANOVA test of forest stage and species. L. racemosa saplings were removed from the analysis of change in dbh, annual change in biomass and relative growth rates due to low sample size. Half normality probability plots were used to assess normality for the linear regressions. Normality plots were used to assess normality for parametric tests. Unless otherwise noted, I used Tukey's Honestly Significantly Difference test for unequal sample sizes for post- hoc comparison. I used a Arcsin |
U.S. Department of the Interior, U.S. Geological Survey
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Last updated: 31 March, 2006 @ 10:55 AM (TJE)