Abstract
Forests are increasingly threatened by climate-change-fuelled cycles of drought, dieback and wildfires. However, for reasons that remain incompletely understood, some forest stands are more vulnerable than others, leaving a patchwork of varying dieback and wildfire risk after drought. Here, we show that spatial variability in forest drought response can be explained by differences in underlying bedrock. Our analysis links geochemical measurements of bedrock composition, geophysical measurements of subsurface weathering and remotely sensed changes in evapotranspiration during the 2011–2017 drought in California. We find that evapotranspiration plummeted in dense forest stands rooted in weathered, nutrient-rich bedrock. By contrast, relatively unweathered, nutrient-poor bedrock supported thin forest stands that emerged unscathed from the drought. By influencing both subsurface weathering and nutrient supply, bedrock composition regulates the balance of water storage and demand in mountain ecosystems. However, rather than enhancing forest resilience to drought by providing more water-storage capacity, bedrock with more weatherable and nutrient-rich minerals induced greater vulnerability by enabling a boom–bust cycle in which higher ecosystem productivity during wet years drives excess plant water demand during droughts.
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Data availability
Data used in this study are available via Hydroshare57 (https://doi.org/10.4211/hs.edbb6ebfbc744186b5800932cd00b507). Landsat data can be accessed at https://www.usgs.gov/landsat-missions/landsat-data-access. PRISM climate data55 can be accessed at https://prism.oregonstate.edu/. NAIP imagery58 can be accessed at https://www.usgs.gov/centers/eros/science/usgs-eros-archive-aerial-photography-national-agriculture-imagery-program-naip. Source data are provided with this paper.
Code availability
Code used to generate figures is available on the Hydroshare repository (https://doi.org/10.4211/hs.edbb6ebfbc744186b5800932cd00b507). Code for geophysical and remote-sensing analyses is available from the corresponding author upon request.
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Acknowledgements
Funding was provided by the National Science Foundation grants EAR-1331939 (C.S.R.) and EAR-2012357 (C.S.R.); National Aeronautics and Space Administration grant NNX15AI08H (R.P.C.); and Natural Sciences and Engineering Research Council of Canada grant RGPIN-2019–05501 (L.S.S.).
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R.P.C. and C.S.R. contributed equally to study design. R.P.C., C.S.R. and L.S.S contributed equally to manuscript preparation and revisions. R.P.C. collected the data, analysed the data and created the figures. K.L.F. and W.J.H. contributed to data analysis and manuscript preparation. C.S.R., L.S.S., S.P. and D.G. contributed to data analysis. N.J.T. contributed to study design and field work. B.A.F. and J.L.H. contributed to field work. W.S.H. contributed to study design, field work and manuscript preparation. All authors reviewed and commented on the manuscript.
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Extended data
Extended Data Fig. 1 Forest dieback in the region around the study sites.
a, Percentage reduction in evapotranspiration from 2014 to 2016 (colorbar) across a 14,876-pixel subset of nearby Landsat pixels (colored squares) with elevations between 1800 and 2400 m but still outside the extent of Pleistocene glaciation. NAIP imagery from 2014 (background) shows differences in vegetation density and white lines represent boundaries between bedrock types (Kbm is Bald Mountain Granite; Kdd is Dinkey Dome Granite; Kbl is Bass Lake Tonalite). b, The distribution of dieback differs markedly between the sites (p < 0.0001 for all three comparisons in a two-sample K-S test after adjusting for multiple comparisons) and collectively spans 94% of the range in dieback spanned by the surrounding region (black).
Extended Data Fig. 2 Topography at study sites.
Study sites are located on ridgetops and therefore have gentle hillslope gradients (with most <30%) (a-c) and have surfaces pointing in multiple directions, leading to wide distributions in slope aspect (d-f).
Extended Data Fig. 4 Vegetation surveys.
Relative abundance of the eight species identified in surveys at the three study sites in Fig. 1 (see Methods). Numbers in parentheses are the number of individuals found at each site. Some trees were not identifiable due to a dieback-related lack of needles or pine cones, so numbers do not sum to 100% at any site.
Extended Data Fig. 5 Calculating unit pore volume.
a, Idealized landscape with geophysical transects (black lines) at surface above weathered soil and saprolite with a vertical gradient in porosity. b, 1×1 m plot and underlying column of soil and saprolite spanned by the survey. c, Unit pore volume (φv) is calculated by integrating geophysics-based porosity (φ(z), gray shaded area) over depth (z) between the base of saprolite (zsap) and the surface (zsurf), where zsap is defined by a threshold VP = 1.1 km/s (see Methods). d, We define unit pore volume as the total pore volume per unit area at the surface. It therefore represents the depth of water required to fill all the void space in the column of soil and saprolite in panel b.
Extended Data Fig. 6 Drought effects on water and energy balances.
a, Variations in evapotranspiration through time at three main study sites with Palmer Drought Severity Index57 (top) and gray band highlighting 2011-2017 California drought. Dashed lines span the 2014 and 2016 interval in which forests experienced the greatest declines in evapotranspiration. Although the drought began in late 2011, forests at our sites did not experience a marked decline in evapotranspiration until 2015. b, Site-to-site differences in evapotranspiration and similarities in climate drive differences in evaporative index (evapotranspiration divided by precipitation) for a given aridity index (potential evapotranspiration divided by precipitation). Points are water-year averages. Bold lines mark Budyko’s energy and water limitations on evapotranspiration when runoff is negligible53. Points above and just beneath the water limit indicate plants used water stored during prior wet years.
Extended Data Fig. 7 Drought-related dieback from NDVI.
NDVI data from 2014 to 2016 generally plot below 1:1 line, indicative of drought-related declines at all 3 sites. Like the ET-ET plot in the main text (Fig. 3c), the data are consistent with a three parameter regression, with a slope, an intercept, and an offset between Bald Mountain and the other two sites (see Extended Data Table 3 for regression parameters, uncertainties, and p values). The statistically significant offset is consistent with a species-related control on forest dieback, as discussed in the main text. In addition, the slope of the relationship is not ≥1 (p < 0.0001), so we can reject the null hypothesis that greater water storage capacity at sites with higher pre-dieback forest productivity compensates for the higher water demand. Hence, dieback from NDVI increases disproportionately with increasing pre-dieback NDVI. Moreover, our results are consistent with bedrock control of dieback, irrespective of whether dieback is quantified using NDVI or ET derived from NDVI.
Supplementary information
Supplementary Information
Supplementary Tables 1–3 and Fig. 1.
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Source Data Fig. 1
Source data for panels b–d and k–n.
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Source Data Extended Data Fig. 1
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Source data for panels a and b.
Source Data Extended Data Fig. 7
Source data for panel a.
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Callahan, R.P., Riebe, C.S., Sklar, L.S. et al. Forest vulnerability to drought controlled by bedrock composition. Nat. Geosci. 15, 714–719 (2022). https://doi.org/10.1038/s41561-022-01012-2
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DOI: https://doi.org/10.1038/s41561-022-01012-2
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