The desire to use sentinel species as early warning indicators of impending climate change effects on entire ecosystems is attractive, but we need to verify that such approaches have sound biological foundations. A recent large-scale warming event in the North Pacific Ocean of unprecedented magnitude and duration allowed us to evaluate the sentinel status of giant kelp, a coastal foundation species that thrives in cold, nutrient-rich waters and is considered sensitive to warming. Here, we show that giant kelp and the majority of species that associate with it did not presage ecosystem effects of extreme warming off southern California despite giant kelp’s expected vulnerability. Our results challenge the general perception that kelp-dominated systems are highly vulnerable to extreme warming events and expose the more general risk of relying on supposed sentinel species that are assumed to be very sensitive to climate change.
The ecological effects of global warming are expected to be large1,2, but are proving difficult and costly to measure. This has led to a growing interest in using sentinel species as early warning indicators of impending climate change effects on entire ecosystems3,4. Identifying sentinel species most likely to be early indicators of climate change would seem a logical way to direct limited monitoring and conservation resources5. If such sentinel species were also foundation species on which other species depend, then their decline could destabilize and collapse entire ecosystems6,7. Coastal marine ecosystems supported by foundation species in temperate seas (for example, kelp forests, seagrass meadows and salt marshes) are reported to be particularly sensitive to ocean warming and low-nutrient availability associated with climate change8, and thus are expected to have been greatly affected by the extraordinary warming that recently occurred off the Pacific coast of North America9.
The ocean warming began in late 2013 when unusually warm waters extending to depths exceeding 100 m were observed in the central North Pacific Ocean with temperature anomalies exceeding three s.d. (∼ 3 °C) above the climate record from 1982–2014 (refs 9, 10, 11). The warming resulted from higher than average sea-level atmospheric pressure that in turn led to below average heat loss from the ocean, weaker winds and less cold-water advection in the upper ocean12. The warm water ‘blob’ moved eastward, and by October 2014 spread to fill the coastal domain from the Gulf of Alaska to the tip of Baja California, Mexico12,13. This phenomenon was followed by severe El Niño conditions, which prolonged the warming through 2015. These changes were unprecedented, possibly since the early 1900s9,11,12 and have been linked to ecological changes in pelagic ecosystems such as reduced nutrients and phytoplankton primary productivity, the appearance of unusual species of zooplankton and fish, and increased mortality in marine birds and mammals9,13.
Time series data of giant kelp forest ecosystems in southern California collected by the Santa Barbara Coastal Long Term Ecological research program provided us with a unique opportunity to examine the effects of the unprecedented warming on an important coastal foundation species, the giant kelp Macrocystis pyrifera, and its associated ecosystem, and to assess the value of kelp forests as sentinels for detecting early signs of climate related impacts. Like most kelps, the growth and survival of Macrocystis are considered highly vulnerable to prolonged conditions of warm, nutrient-poor water14,15 and such conditions have been implicated as the cause for massive regional declines16,17. The demography and physiology of Macrocystis make it potentially well suited as a climate sentinel because of its rapid growth (2% dry mass per day)18, high biomass turnover (6–7 times per year)18 and relatively high nitrogen demand (>1 μmol l−1 needed to sustain growth)19; yet, limited capacity for internal nitrogen storage (<3 weeks)20 should cause its biomass to respond quickly to prolonged unfavourable growing conditions associated with climate change.
Surprisingly, fluctuations in the biomass of giant kelp and much of its associated biota remained within historical ranges despite 24 months of above average temperatures and below average nutrients. The resilience of giant kelp to the unprecedented warming not only highlights the limitations in our understanding of the ecology of kelp-dominated ecosystems, but also questions their general use as early indicators of climate change.
We observed the first signs of prolonged warming of bottom waters within kelp forests of the Santa Barbara Channel in late December 2013 when temperature anomalies turned conspicuously positive (Fig. 1a). Positive monthly temperature anomalies persisted through December 2015 with daily deviations as high as +5.8 °C and monthly deviations averaging as much as +4.6 °C. The unprecedented extent of the warming is evidenced by the occurrence and duration of unusually warm water events in 2014–2015 compared with earlier in the time series (Fig. 1b). Fifty-eight per cent of the days during 2014 and 2015 (423 of 730 days) met the criteria of a marine heatwave (that is, five or more consecutive days when the mean temperature is warmer than the 90th percentile)21 compared with only 3.4% (162 of 4,748 days) during the previous 13 years. Moreover, the duration of heatwaves averaged three times longer during 2014–2015 (mean=39 days, maximum=151 days, n=11) compared with 2001–2013 (mean=12 days, maximum=30 days, n=13).
Anomalies in bottom-water nitrate concentrations were negative in every month during 2014 and 2015 (Fig. 1c). Moreover, 2014–2015 was characterized by three prolonged events with critically low nitrate (that is,<1 μmol l−1) lasting 50, 156 and 195 days, respectively, which collectively encompassed 54% of the 2-year period (Fig. 1d). In contrast, events of<1 μmol l−1 lasting at least 21 days (=maximum duration that growth in giant kelp can be sustained on internal nitrogen reserves20) were typically much shorter in duration in 2001–2013, and collectively accounted for only 7% of the days during this period.
Large storm waves tear out giant kelp and greatly alter kelp forest communities14,15. Large winter swells coincided with the warm, nutrient-poor water associated with the severe El Niños of 1982–1983 and 1997–1998 (refs 22, 23), which made it difficult to disentangle the effects of ocean warming and low nutrients on kelp forests from those caused by wave disturbance16. Unlike ocean temperature and nutrients, the wave climate in the Santa Barbara Channel during 2014 and 2015 was largely unremarkable. The largest monthly anomaly in maximum significant wave height during the recent warm period was 0.54 m in October 2014 compared with 1.2 m in March 1983 and 2.3 m in February 1998 (Fig. 2a). Moreover, larger swells were recorded at our kelp forest study sites during the cool years of 2006 and 2008 than in the anomalously warm years of 2014 and 2015 (Fig. 2b). Thus, unlike during previous warming episodes of the latter twentieth century, anomalous disturbance from waves was not a confounding factor during the extreme warming in 2014–2015.
The community structure of kelp forests in the region varied substantially throughout the 15-year time series, but surprisingly, large responses to the unprecedented warm, nutrient-poor conditions were not obvious for most components of the community. In particular, we did not detect a dramatic response by giant kelp. Instead, we observed considerable inter-annual variability in its summer biomass with values for 2014 and 2015 within or slightly below the range of values recorded during the cooler years of the time series (Fig. 3a). Overall, kelp biomass decreased significantly during the 15-year record, but this decline was unrelated to anomalies in temperature in the previous year (Table 1, Supplementary Fig. 1a). Understory algae that grow on the sea floor beneath the canopy of giant kelp, and mobile reef fishes were even more unresponsive to the unprecedented warming, as their biomass did not vary significantly over time and remained well within the range of values observed during previous years (Fig. 3b,f; Table 1, Supplementary Fig. 1b,f). Moreover, multivariate analyses showed that the algal and fish assemblages did not differ appreciably between the cool and warm periods (Supplementary Fig. 2a,c). Instead, the species composition of understory algae shifted gradually through time while that of reef fishes exhibited no consistent trend over the record.
Benthic sessile invertebrates that feed on plankton and other suspended matter in the water column constitute the largest consumer group in the kelp forest. Their biomass decreased significantly over the study period (Fig. 3c), but their decline was independent of the anomalously warm conditions (Table 1, Supplementary Fig. 1c). The species assemblage of sessile invertebrates changed gradually over the course of the time series and showed a modest (21.3%) dissimilarity between the cool (2001–2013) and warm (2014–2015) periods (Supplementary Fig. 2b, Supplementary Table 1).
The biomass of sea urchins, the most important grazers in kelp forests worldwide24, showed no consistent trend over time (Fig. 3d, Table 1). Moreover, neither the biomass of giant kelp nor understory algae explained any of the year-to-year variation in sea urchin biomass (neither variable met the 0.15 significance level for entry into a stepwise multiple regression model regardless of whether data for kelp and understory algae were derived from the same year as sea urchins or the previous year). Instead sea urchin biomass was negatively correlated with anomalies in bottom temperature (Table 1, Supplementary Fig. 1d) Sea urchin biomass reached its lowest level in 2015 when it declined by 50% from 2014. This abrupt decline is consistent with a rapid response to extreme warming that occurred during the previous 12 months. Indeed, our observations suggested that this abrupt decline resulted from an infectious disease (as evidenced by visible lesions on the epidermis) that is known to spread rapidly during warm periods25. The absence of a large positive response by giant kelp and understory algae coinciding with this decrease in sea urchin biomass, and the generally poor correlation between sea urchins and their algal food supply throughout the time series, emphasizes the complexity of biotic and abiotic interactions in kelp-dominated systems26.
The most dramatic response to warming was observed in sea stars, an important group of invertebrate predators. Unlike other components of the kelp forest community, sea stars were increasing before the onset of warming in 2014, which accounted for an overall increasing trend during the time series (Fig. 3e, Table 1). However, in 2014 an epidemic outbreak of wasting disease led to mass mortalities of at least 20 species of sea stars from Alaska to Mexico27. Sea star biomass in the kelp forests off Santa Barbara declined to near zero by 2015. Museum specimens show that the densovirus linked to this disease has been present on the Pacific coast of North America for at least 72 years27 and the anomalously warm water temperatures have been implicated in increasing its spread and the mortality rate in sea stars28. This implication is consistent with the negative relationship that we observed between sea star biomass and bottom temperature anomalies (Table 1, Supplementary Fig. 2e). So far the mass mortalities of sea stars have not led to corresponding increases in their prey. The biomass of piddocks and shelled gastropods, favourite prey of sea stars, did not change appreciably in the 2 years following the disappearance of sea stars (Supplementary Fig. 3), although increases in these longer-lived animals may be expected in the future if sea stars do not recover.
Giant kelp populations are naturally quite variable, so changes in kelp forests can easily be misinterpreted unless viewed in the context of long-term data29. Longer and more spatially comprehensive records of giant kelp and sea surface temperature (SST) obtained from satellite imagery confirm the patterns documented by divers and moored sensors at our study sites. Large seasonal and interannual fluctuations in giant kelp biomass characterized all of southern California from 1984–2015 (Fig. 4a). However, negative-kelp anomalies during 2014–2015 from Santa Barbara to the Mexican border in San Diego were within the range observed during the 32-year time series despite unprecedented positive anomalies in ocean temperatures during this period (Fig. 4b). This result is quite surprising given giant kelp’s reported sensitivity to such conditions16,17 and stands in contrast to reports from other kelp systems showing sharp declines in response to warming conditions30,31,32. The location of our study within giant kelp’s range offers one possible explanation for the difference; southern California, and Santa Barbara in particular, does not represent either the geographical or thermal limit for the species in the northeast Pacific14,15 although San Diego is on average 1–4 °C warmer than Santa Barbara and closer to giant kelp’s thermal limit (Supplementary Fig. 4). Nevertheless, giant kelp populations are highly adapted to local nutrient conditions33 and the potential for rapid dispersal from distant populations that are better adapted to sudden changes in local conditions is limited34. Thus, similar to that shown for other habitat forming seaweeds35, we would expect giant kelp populations far from the range edge to be equally sensitive to large and sustained anomalies in temperature and nutrients such as those associated with the recent warming event.
Anthropogenic climate change is predicted to cause the extinction of thousands of species over the next century1,2 so understanding the responses of species to climate change is perhaps the most pressing issue facing ecologists today. Anomalous environmental conditions offer exceptional opportunities to test our expectations for ecosystem responses to climate change. The lack of an expected response to an extreme event, as in our study, reveals our limited ability to predict responses to longer term changes. Such limits on our forecasting ability underscore the key role of long-term data in detecting the effects of climate change on ecosystems as they occur29,36, prompting calls for the need to identify and monitor sentinel species3,4,5. Indeed, given the cost of collecting long-term data, efforts to focus research on the most sensitive and vulnerable species seem wise. However, our results expose the potential dangers of relying on easily measured iconic species with supposed sensitive traits as sentinels for evaluating ecosystem responses to climate change. We suggest that in the absence of an ability to reliably predict sentinel species, broader spectrum ecological monitoring is necessary to inform us of the status of biodiversity in the face of climate change.
We collected oceanographic and ecological data from 2001–2015 at nine kelp forest sites located at 7–10 m depth along an 80 km stretch of the mainland coast of the Santa Barbara Channel in southern California, USA (Supplementary Fig. 5).
Sea temperature was measured every 10 min using loggers (Stowaway Onset tidbits, accuracy±0.2 °C; Onset Computer, Bourne, Massachusetts, USA) fastened to the bottom at each site. Longer records of ocean temperature from 1982–2015 were obtained for the Santa Barbara region from the National Climatic Data Center Optimal Interpolation Sea Surface Temperature data. These data combine measurements from several sources including ship, buoys and Advanced Very High Resolution Radiometer satellite images from January 1982–December 2015 to produce a daily averaged data set with a resolution of 0.25 °C. The values shown in Fig. 4b represent the mean of the pixels that encompass the coastal waters offshore of Santa Barbara, Los Angeles and San Diego counties.
The nutrient considered to most often limit primary production in the Santa Barbara Channel and elsewhere in southern California is nitrogen in the form of nitrate, which can be predicted from temperature37. We modelled nitrate concentration at our sites as a function of bottom temperature using the exponential relationship developed by Fram et al.38 for the Santa Barbara Channel.
We used the maximum value of the significant wave height (Hs) during each month of the 15-year time series as a measure of wave disturbance. Hs represents the mean of the largest one-third of the waves recorded during a 30-min sampling period and the maximum Hs has been shown to be significantly correlated with the amount of kelp biomass loss18,39,40. Hs data for the period 2001–2015 were obtained from the Coastal Data Information Program’s nowcast wave-propagation model for locations nearest to each of the nine kelp forest sites40. The model provides hourly estimates of Hs along a 10 m isobath at an 800 m longshore resolution. Longer term records of Hs (1980–2015) used to compare the wave climate during our study with that during the severe El Niños of the later 20th century were obtained from the Wave Information Studies hindcast model nearest the location of the Harvest platform buoy (Station 46218) located offshore in the Santa Barbara Channel (34.454 N 120.782 W). The Harvest buoy provided additional Hs data from 2012–2015.
Monthly values of bottom temperature, bottom nitrate and maximum Hs were calculated for each of the nine kelp forest sites and were averaged to produce a regional mean value for each day of the time series. Regional daily means were averaged to produce regional monthly means. Regional monthly anomalies for bottom temperature and bottom nitrate were calculated as the difference between the regional mean value for a given month in a given year and the 15-year average for that month. Monthly anomalies for maximum Hs used to compare the wave climate during the recent warming in 2014–2015 with that during the 1982–1983 and 1997–1998 El Niños were calculated as the difference between the mean obtained using modelled hindcast and buoy data from Harvest Platform for a given month in a given year and the 36-year average (1980–2015) for that month. To further characterize the oceanographic conditions at our study sites we applied Hobday et al.’s hierarchical approach for defining marine heatwaves21 to the bottom temperature data and calculated the occurrence and duration of heatwaves in each year of the time series. We estimated low nitrate events as periods when a mean daily nitrate concentration of 1 μmol l−1 persisted for at least 21 days. The rationale for this definition is based on previous studies that concluded concentrations of nitrate<1 μmol l−1 are not sufficient to support normal growth in Macrocystis19 and its internal nitrogen reserves become exhausted within 21 days without any external supplies20.
Annual community surveys of marine flora and fauna were performed by divers using SCUBA in late July to early August each year. Sampling was done within 34 permanently located 40 m × 2 m plots distributed among the nine kelp forest sites. The density and size of giant kelp, large solitary understory algae, large mobile invertebrates and reef-associated fishes were measured within each plot (Supplementary Table 2). Smaller mobile invertebrates and solitary algae were counted within six 1 m2 quadrats placed at 8 m intervals along the 40 m axis of each plot. The per cent cover of sessile invertebrates and understory algae that are impractical to count as individuals was measured at 80 uniformly spaced points within each plot. Data on size and abundance of each species counted in the surveys were converted into biomass using species specific relationships developed for algae41,42, invertebrates43 and fish44,45,46,47 in the region. Mean biomass values for the different taxonomic groups examined were calculated for each of the nine sites and then averaged to produce a regional mean value for each year.
Longer more spatially comprehensive records of giant kelp canopy biomass were estimated at 30-m resolution from 1984–2015 using multispectral Landsat 5 and 7 Thematic Mapper satellite imagery following procedures developed by Cavanaugh et al.48. Kelp canopy biomass was estimated using the observed relationship between diver-estimated kelp canopy biomass at our study sites and Landsat pixel kelp fraction. Cloud-free imagery allowed kelp biomass to be estimated approximately monthly. Seasonal canopy biomass determinations for each 30 m × 30 m pixel along the mainland coast of the counties of Santa Barbara, Los Angeles and San Diego Channel were summed to produce a value of kelp canopy biomass for each county, for each season of the 32-year time series.
The primary focus of our study was on detecting regional responses to a large-scale warming event. Therefore, our analyses involved models using regional means averaged across the nine sites rather than estimates of the mean and variance of variables from the time series of individual sites (for example, the regional mean and variance in the relationship between local kelp biomass and local temperature that would be derived from a mixed effects model). Thus we evaluated the amount of variation in the regional summer biomass of the different functional groups of kelp forest species that was explained by anomalous warming using stepwise multiple regression with a threshold level of significance=0.15 for entry into the model (SAS 9.4, SAS Institute Inc., Cary, NC, USA). Annual anomalies in bottom temperature for the 12-month period preceding the summer measurements of biomass were used as an independent variable in the regression analysis of each functional group. Year was included as an additional independent continuous variable to account for temporal trends not explained by anomalous oceanographic conditions. Multi-collinearity of the two independent variables was low in all cases; condition indices were<26 and variance inflation factors<2 for all analyses.
Differences in the species structure of understory algae, sessile invertebrates and reef fishes before and after the extreme warming were analysed using multidimensional scaling49 and permutation-based analysis of variance using Type III sums of squares50 followed by similarity percentages (SIMPER) to decompose the contributions of individual species leading to dissimilarities (Bray–Curtis) between the cool (2001–2013) and warm (2014–2015) periods. While multidimensional scaling plots provide an intuitive means of evaluating differences in species assemblages among years, the statistical significance of differences between cool and warm periods as determined by permutation-based analysis of variance should be viewed with caution due to the unbalanced replication of years between the two periods.
Data collected by SBC LTER that support the findings of this study are available with the following identifiers: kelp forest species biomass doi:10.6073/pasta/449a810468445ef1ce60769466cd1fad; bottom temperature: doi:10.6073/pasta/c3ec3193ba97e7670b532cfbbe1632f9; Landsat kelp biomass (1984–2011) doi:10.6073/pasta/329658f19d5e61dda0be5ee883cd1c41; Landsat kelp biomass (2012–2015) available from authors. Access to these data require users to accept SBC LTER’s data use agreement.
SST and swell height data used in this study are publically available at: SST http://www.ncdc.noaa.gov/oisst/; CDIP swell height http://cdip.ucsd.edu/; Wave Information Studies hindcast model http://wis.usace.army.mil/; Platform Harvest swell height http://www.ndbc.noaa.gov/station_history.php?station=46218.
How to cite this article: Reed, D. et al. Extreme warming challenges sentinel status of kelp forests as indicators of climate change. Nat. Commun. 7, 13757 doi: 10.1038/ncomms13757 (2016).
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Pereira, H. M. et al. Scenarios for global biodiversity in the 21st century. Science 330, 1496–1501 (2010).
Thomas, C. D. et al. Extinction risk from climate change. Nature 427, 145–148 (2004).
Schwing, F. B., Peterson, W. T., Cyr, N. & Osgood, K. E. in The Future of Fisheries Science in North America (eds Beamish R. J. & Rothschild, B. J.) 621–636 (Springer Netherlands, 2009).
Merzouk, A. & Johnson, L. E. Kelp distribution in the northwest Atlantic Ocean under a changing climate. J. Exp. Mar. Biol. Ecol. 400, 90–98 (2011).
Caro, T. Conservation by Proxy: Indicator, Umbrella, Keystone, Flagship, and Other Surrogate Species Island Press (2010).
Dayton, P. K. in Proceedings of The Colloquium on Conservation Problems in Antarctica (ed. Parker, B. C.) 81–96 (Allen Press, 1972).
Ellison, A. M. et al. Loss of foundation species: consequences for the structure and dynamics of forested ecosystems. Front. Ecol. Envir. 3, 479–486 (2005).
Wong, P. P. et al. in Climate change 2014: Impacts, adaptation, and vulnerability. Part A: global and sectoral aspects. Contribution of working group II to the fifth assessment report of the intergovernmental panel on climate change (eds Field, C. B. et. al.) 361–409 (Cambridge University Press, 2014).
Di Lorenzo, E. & Mantua, N. Multi-year persistence of the 2014/15 North Pacific marine heatwave. Nat. Clim. Change 6, 1042–1047 (2016).
Freeland, H. & Whitney, F. Unusual warming in the Gulf of Alaska. PICES Press 22, 51 (2014).
Peterson, W., Robert, M. & Bond, N. The warm blob—Conditions in the northeastern Pacific Ocean. PICES Press 23, 36 (2015).
Bond, N. A., Cronin, M. F., Freeland, H. & Mantua, N. Causes and impacts of the 2014 warm anomaly in the NE Pacific. Geophys. Res. Lett. 42, 3414–3420 (2015).
Kintisch, E. The ‘Blob’ invades Pacific, flummoxing climate experts. Science 348, 17–18 (2015).
Graham, H. H., Vasquez, J. A. & Buschmann, A. H. Global ecology of the giant kelp Macrocystis: from ecotypes to ecosystems. Oceanogr. Mar. Biol. Ann. Rev. 45, 39–88 (2007).
Schiel, D. R. & Foster, M. S. The biology and ecology of giant kelp forests University of California Press (2015).
Dayton, P. K. & Tegner, M. J. in Global Ecological Consequences of the 1982-83 El Niño-Southern Oscillation (ed. Glynn, P. W.) 433–472 (Elsevier Oceanography Series No. 52, 1989)..
Johnson, C. R. et al. Climate change cascades: shifts in oceanography, species' ranges and subtidal marine community dynamics in eastern Tasmania. J. Exp. Mar. Biol. Ecol. 400, 17–32 (2011).
Reed, D. C., Rassweiler, A. & Arkema, K. K. Biomass rather than growth determines net primary production by giant kelp. Ecology 89, 2493–2505 (2008).
Gerard, V. A. In situ rates of nitrate uptake by giant kelp, Macrocystis pyrifera (l.) C. Agardh: tissue differences, environmental effects, and predictions of nitrogen-limited growth. J. Exp. Mar. Biol. Ecol. 62, 211–224.
Gerard, V. A. Growth and utilization of internal nitrogen reserves by the giant kelp Macrocystis pyrifera in a low-nitrogen environment. Mar. Biol. 66, 27–35 (1982).
Hobday, A. J. et al. A hierarchical approach to defining marine heatwaves. Prog. Oceanog. 141, 227–238 (2016).
Dayton, P. K. & Tegner, M. J. Catastrophe, storms, El Niño, and patch stability in a southern California kelp community. Science 224, 283–285.
Edwards, M. S. Estimating scale-dependency in disturbance impacts: El Niños and giant kelp forests in the northeast Pacific. Oecologia 138, 436–447 (2004).
Dayton, P. K. Ecology of kelp communities. Ann. Rev. Ecol. Syst 16, 215–245 (1985).
Lester, S. E., Tobin, E. D. & Behrens, M. D. Disease dynamics and the potential role of thermal stress in the sea urchin Strongylocentrotus purpuratus. Can. J. Fish. Aquat. Sci. 64, 314–323 (2007).
Wernberg, T. M. et al. Decreasing resilience of kelp beds along a latitudinal temperature gradient: potential implications for a warmer future. Ecol. Lett. 13, 685–694 (2010).
Hewson, I. et al. Densovirus associated with sea-star wasting disease and mass mortality. Proc. Natl Acad. Sci. USA 111, 17278–17283 (2014).
Eisenlord, M. E. et al. Ochre star mortality during the 2014 wasting disease epizootic: role of population size structure and temperature. Phil. Trans. R. Soc. B 371, 20150212 (2016).
Reed, D. C., Rassweiler, A. R., Miller, R. J., Page, H. M. & Holbrook, S. J. The value of a broad temporal and spatial perspective in understanding dynamics of kelp forest ecosystems. Mar. Fresh. Res. 67, 14–24 (2016).
Wernberg, T. et al. An extreme climatic event alters marine ecosystem structure in a global biodiversity hotspot. Nat. Clim. Change 3, 78–82 (2013).
Filbee-Dexter, K., Feehan, C. & Scheibling, R. E. Large-scale degradation of a kelp ecosystem in an ocean warming hotspot. Mar. Ecol. Prog. Ser. 543, 141–152 (2016).
Wernberg, T. et al. Climate-driven regime shift of a temperate marine ecosystem. Science 353, 169–172 (2016).
Kopczak, C. D., Zimmerman, R. C. & Kremer, J. N. Variation in nitrogen physiology and growth among geographically isolated populations of the giant kelp, Macrocystis pyrifera (Phaeophyta). J. Phycol. 27, 149–158 (1991).
Reed, D. C. et al. in Marine Metapopulations (eds Kritzer, J. P. & Sale, P. F.) 352–386 (Academic Press, 2006).
Bennett, et al. Central and rear-edge populations can be equally vulnerable to warming. Nat. Commun. 6, 10280 (2015).
Lindenmayer, D. B. & Likens, G. E. Adaptive monitoring: a new paradigm for long-term research and monitoring. Trends Ecol. Evol. 24, 482–486 (2009).
Zimmerman, R. C. & Kremer, J. N. Episodic nutrient supply to a kelp forest ecosystem in Southern California. J. Mar. Res. 42, 591–604.
Fram, J. P. et al. Physical pathways and utilization of nitrate supply to the giant kelp Macrocystis pyrifera. Limnol. Oceanogr. 53, 1589–1603 (2008).
Reed, D. C. et al. Wave disturbance overwhelms top-down and bottom-up control of primary production in California kelp forests. Ecology 92, 2108–2116 (2011).
Bell, T. W., Cavanaugh, K. C., Reed, D. C. & Siegel, D. A. Geographic variability in the controls of biomass dynamics of giant kelp. J. Biogeogr. 42, 2010–2021 (2015).
Reed, D. C., Rassweiler, A. R. & Arkema, K. Density derived estimates of standing crop and net primary production in the giant kelp Macrocystis pyrifera. Mar. Biol. 156, 2077–2083 (2009).
Harrer, S. L., Reed, D. C., Miller, R. J. & Holbrook, S. J. Patterns and controls of the dynamics of net primary production by understory macroalgal assemblages in giant kelp forests. J. Phycol. 49, 248–257 (2013).
Reed, D. C., Nelson, J. C., Harrer, S. L. & Miller, R. J. Estimating biomass of benthic kelp forest invertebrates from body size and percent cover data. Mar. Biol. 163, 1–6 (2016).
Quast, J. C. Fish fauna of the rocky inshore zone. Cal. Fish Game Fish Bull. 139, 35–55 (1968).
Quast, J. C. Estimates of the population and standing crop of fishes. Cal. Fish Game Fish Bull. 139, 57–79 (1968).
DeMartini, E. E., Barnett, A. M., Johnson, T. D. & Ambrose, R. F. Growth and reproduction estimates for biomass-dominant fishes on a southern California artificial reef. Bull. Mar. Sci. 55, 484–500 (1984).
Love, M. S. Certainly More Than You Want to Know About The Fishes of The Pacific Coast: A Postmodern Experience Really Big Press (2011).
Cavanaugh, K. C., Siegel, D. A., Reed, D. C. & Dennison, P. E. Environmental controls of giant-kelp biomass in the Santa Barbara Channel, California. Mar. Ecol. Prog. Ser. 429, 1–17 (2011).
Clarke, K. R. & Gorley, R. N. PRIMER V6: User Manual/Tutorial PRIMER-E Ltd (2006).
Anderson, M. J., Gorley, R. N. & Clarke, K. R. PERMANOVA+ for PRIMER: Guide to Software and Statistical Methods PRIMER-E Ltd (2008).
The research was supported by the U.S. National Science Foundation’s Long Term Ecological Research program (OCE 9982105, 0620276 & 1232779) and by the National Aeronautics and Space Administration Biodiversity and Ecological Forecasting program (NASA Grant NNX14AR62A), the Bureau of Ocean and Energy Management Ecosystem Studies program (BOEM award MC15AC00006) and NOAA in support of the Santa Barbara Channel Biodiversity Observation Network. S. Schroeter assisted with the multivariate analyses.
The authors declare no competing financial interests.
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Reed, D., Washburn, L., Rassweiler, A. et al. Extreme warming challenges sentinel status of kelp forests as indicators of climate change. Nat Commun 7, 13757 (2016). https://doi.org/10.1038/ncomms13757
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