Is Australia shooting itself in the foot with reef port expansions?


Ove Hoegh-Guldberg, Global Change Institute, University of Queensland.  From The Conversation, March 14, 2014

With the approval of dredging as part of the Abbot Point port expansion, Australia has given the green light to an increase in coal exports. While opposition to the plan has focused primarily on the effects of dumping dredge spoil near the Great Barrier Reef, climate change has been missing from the discussion.

Increasing coal exports will play a significant part in the decline of the Great Barrier Reef, and will prove to be a very uneconomical decision for Australia.

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Scientists predict US$2trn cost to ocean economies, March 22, 2012.  Scientists at the Stockholm Environment Institute (SEI) have released a new study that has placed the effects of climate change on the world’s ocean ecosystems under the spotlight. They predict climate change alone could reduce the economic value of key ocean services by up to US$2trn a year by 2100.

The scientists are now calling for a global, integrated approach to protect oceans from converging threats.
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Revealing the oceans

“The visual nature of the project will also help bridge the gap between scientific knowledge and public awareness,” Professor Hoegh-Guldberg

Diver deploying 360 degree camera to obtain Catlin Seaview Survey images.

Press release, University of Queensland,

A pioneering scientific expedition that will document the health of coral on the Great Barrier Reef will be undertaken as a joint venture between global technology giant Google, the UQ Global Change Institute, not-for-profit organisation Underwater Earth and insurance company Catlin.

The Catlin Seaview Survey, announced in Singapore today, aims to carry out the first comprehensive study of the composition and health of Reef coral to an unprecedented depth range (0-100m).  Continue reading

Pesticides and the Great Barrier Reef: Extensive new data and analysis and increased concerns (a note from Jon Brodie)

As a result of an extensive research and monitoring program funded by the Queensland and Australian Governments over the last 5 years  a greatly better understanding of the risks to Great Barrier Reef ecosystems from pesticide residues is now available and in the process of being published in the scientific literature. Most of the papers are or will be published in special issues of Marine Pollution Bulletin and Agriculture Ecosystems and the Environment. Some of the MPB papers are already published online and the rest from both issues will follow over the next few months. While the complete set is still uncertain (due to reviewing still in progress) the following are already out:

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Bubbling sea signals severe coral damage this century

Dobu Island in Papua New Guinea has active underwater fumaroles (Jennifer Marohasy posted on it a few years back) that seep high concentrations of CO2 into the environment, in turn acidifying the surrounding ocean. These vents have been active for at least 50 years: according to village elders  these seeps have existed at that location throughout their life (the local traditional site name “Illi Illi Bua Bua” translates to “Blowing Bubbles”).

Katherina Fabricius and a collaboration of scientists have published an amazing article in the journal Nature Climate Change looking at a gradient across these seeps and the impacts on coral reef ecosystems. The results are striking:

Seascapes at a, control site (‘low pCO2’: pH~8.1), b, moderate seeps (‘high pCO2’: pH 7.8–8.0), and c, the most intense vents (pH<7.7), showing progressive loss of diversity and structural complexity with increasing pCO2. d, Map of the main seep site along the western shore of Upa-Upasina (marked as grey; map: Supplementary Fig. S1). Colour contours indicate seawater pH, and the letters indicate the approximate locations of seascapes as shown in a–c.

“The implications of the observed ecological changes for the future of coral reefs are severe. The decline in structurally complex framework-forming corals at lowered pH is likely to reduce habitat availability and quality for juvenile fish and many invertebrates. The low coral juvenile densities (including those of Porites) probably slows coral recovery after disturbance, suggesting reduced community resilience. The loss of crustose coralline algae that serve as settlement substratum for coral larvae probably impedes larval recruitment, and the doubling of non-calcareous macroalgae reduces the available space for larvae to settle. Susceptibility to storm breakage would also increase, if internal macrobioeroder densities in massive Porites are indicative of borer densities in other coral taxa and reef substrata.”

Bearing in mind these caveats, our data nevertheless suggest that tropical coral reefs with high coral cover can still exist at seawater pH of 7.8 (750 ppm pCO2), albeit with severe losses in biodiversity, structural complexity and resilience. As pH declines from 8.1 to 7.8 units, the loss of the stenotopic fast-growing structurally complex corals progressively shifts reef communities to those dominated by slow-growing, long-lived and structurally simple eurytopic massive Porites (Fig. 1a,b).

Reef development ceases at 7.7 pH units (980 ppm pCO2), suggesting these values are terminal thresholds for any form of coral reef development.  T

The big question that remains is how elevated sea temperatures will interact with the effects of acidification.  So far, it doesn’t look hopeful (Anthony et al. 2008). More from the BBC and Sciencedaily. Unsurprisingly, no word from Andrew Bolt, Anthony Watts or Jennifer Marohasy.

Bolt distorts facts about the Great Barrier Reef again: doesn’t understand or wilful distortion?

Update: Andrew Bolt is at it again.  Either he doesn’t understand the science or he is wilfully distorting the information surrounding the impact of climate change on coral reefs.

See also this previous posting (Bolt gets it wrong again) and this post on record mass coral bleaching occurring right now off Western Australia.

Update: this piece was first published back on Feb 10th, 2009 – I thought it would be worth bringing up to the top to highlight Bolt’s ongoing war against science. Continue reading

Climate Change Will Lead to the Extinction of Coral Reef Fish

One of the many factors causing the global loss of reef building corals is anthropogenic climate change, which is slowly warming the world’s oceans. When summertime temperatures are warmer than usual, corals can die from “bleaching” and disease outbreaks. This in turn is devastating for the countless organisms that inhabit coral reefs.

A new paper (Graham et al 2011) by an international team of marine scientists describes a framework to predict and measure the impacts of coral loss on fish populations. They created an “extinction risk index” for reef fish, based on the habitat requirements, feeding ecology and other traits of each species. For example, obligate corallivores, fish that feed on corals such as butterflyfish, were scored as highly sensitive. In all, 56 of the 134 coral fish species studied were found to be at risk from loss of their habitat, shelter and food sources caused by climate change. Those most in jeopardy were the smaller fishes with specialized eating and sheltering habits. One of the interesting findings from this exercise is that fish predicted to be vulnerable to climate change are not vulnerable to over-harvesting, and vice versa.

The team then tested their model by comparing its predictions to documented fish extinctions caused by a massive coral bleaching event that occurred in 1998 in the Indian ocean in which whole landscapes of corals died off. The fish species predicted to be the most sensitive to such habitat degradation experienced the greatest population losses.

Taken broadly, their results indicate that more than a third of coral reef fish species are in jeopardy of local extinction from the impacts of climate change.

“The loss of particular species can have a critical effect on the stability of an entire ecosystem – and our ability to look after coral reefs depends on being able to predict which species or groups of fish are most at risk,” explains lead author Dr. Nick Graham of the ARC Centre of Excellence in Coral Reef Studies and James Cook University. “Until now, the ability to do this has been fairly weak.”

“Where there is a widespread death of corals from a climate-driven event such as bleaching, the fish most affected are the ones that feed or shelter almost exclusively on coral.”

The study does, however, offer encouragement by showing that the fish most at risk from climate change are seldom those most at risk from overfishing or other direct human impacts, pointing to scope to manage reef systems and fishing effort in ways that will protect a desirable mix of fish species that promote ecosystem stability.

Dr. Tim McClanahan of the Wildlife Conservation Society explains:

Critically, the species of fish that are important in controlling seaweeds and outbreaks of deleterious invertebrate species are more vulnerable to fishing than they are to climate change disturbances on coral reefs. This is encouraging, since local and regional commitment to fisheries management action can promote coral recovery between disturbances such as storms and coral bleaching events.

One thing I really like about the paper is that it focuses on the impacts of habitat loss on reef inhabitants. Corals are dying in droves from climate change and local impacts like runoff from coastal deforestation, but reef scientists are not worried about coral extinctions. It is reef ecosystems that we are going to lose along with all the ecological splendor and economic value that is based on them.

Their paper, “Extinction vulnerability of coral reef fishes,” by Nicholas A. J. Graham, Pascale Chabanet, Richard D. Evans, Simon Jennings , Yves Letourneur, M. Aaron MacNeil, Tim R. McClanahan, Marcus C. Öhman, Nicholas V. C. Polunin and Shaun K. Wilson, appears in the latest issue of the journal Ecology Letters.

New study finds growth of corals on the Belize Barrier Reef is slowing

A new study just published in PLos One (Castillo et al 2010) indicates massive corals (Siderastrea sideria) on the outer reefs of the Belizean Barrier Reef are growing more slowly than they did during the early and middle 20th century.

Lead author Karl Castillo (a post doc in my lab) is from southern Belize near the reefs where the study was conducted.  He and my UNC colleague Dr. Justin Ries took core samples from 13 massive starlet corals, a species that can grow to sizes of more than 1 meter across. They then measured the thickness of growth bands in the coral samples.

Core sections represent the most recent years of skeletal extension for Siderastrea siderea from the (A) forereef [core FR-12], (B) backreef [core BR-06], and (C) nearshore reef [core NS-14]. Numbers correspond to year of paired high-low density annual growth bands. Asterisks correspond to the annual growth bands formed during the 1998 coral bleaching event.


Natural and anthropogenic stressors are predicted to have increasingly negative impacts on coral reefs. Understanding how these environmental stressors have impacted coral skeletal growth should improve our ability to predict how they may affect coral reefs in the future. We investigated century-scale variations in skeletal extension for the slow-growing massive scleractinian coral Siderastrea siderea inhabiting the forereef, backreef, and nearshore reefs of the Mesoamerican Barrier Reef System (MBRS) in the western Caribbean Sea.

Methodology/Principal Findings

Thirteen S. siderea cores were extracted, slabbed, and X-rayed. Annual skeletal extension was estimated from adjacent low- and high-density growth bands. Since the early 1900s, forereef S. siderea colonies have shifted from exhibiting the fastest to the slowest average annual skeletal extension, while values for backreef and nearshore colonies have remained relatively constant. The rates of change in annual skeletal extension were −0.020±0.005, 0.011±0.006, and −0.008±0.006 mm yr−1 per year [mean±SE] for forereef, backreef, and nearshore colonies respectively. These values for forereef and nearshoreS. siderea were significantly lower by 0.031±0.008 and by 0.019±0.009 mm yr−1 per year, respectively, than for backreef colonies. However, only forereef S. siderea exhibited a statistically significant decline in annual skeletal extension over the last century.


Our results suggest that forereef S. siderea colonies are more susceptible to environmental stress than backreef and nearshore counterparts, which may have historically been exposed to higher natural baseline stressors. Alternatively, sediment plumes, nutrients, and pollution originating from watersheds of Guatemala and Honduras may disproportionately impact the forereef environment of the MBRS. We are presently reconstructing the history of environmental stressors that have impacted the MBRS to constrain the cause(s) of the observed reductions in coral skeletal growth. This should improve our ability to predict and potentially mitigate the effects of future environmental stressors on coral reef ecosystems.

They found that over the last 90 years, growth rates for corals in the forereef zone shifted from being the fastest of the three zones to the slowest, while the skeletal extension rates of corals closer to the coast remained relatively stable.

“Massive starlet corals are like old-growth trees in a forest, and the annual extension bands in these core samples tell a cautionary tale,” said the study’s lead author, Karl Castillo, Ph.D., a postdoctoral research associate in the marine sciences department in the UNC College of Arts and Sciences. “The forereef corals used to have the greatest linear extension, but since early last century their growth has clearly been stunted.”

“This suggests that backreef and nearshore corals may be accustomed to stressful conditions because of their regular exposure to high environmental stress,” he said. “But forereef corals — which have probably been less conditioned by baseline natural stressors — appear to be more susceptible to recent human-made impacts such as ocean warming.”

Listen to an interview with Glen De’ath about similar findings on Australia’s Great Barrier Reef here.

Coral Reef Baselines

The pristine or natural state of a population or community is called the baseline in conservation biology. A baseline serves as a guide for setting conservation and restoration targets. Unfortunately, scientists rarely have reliable information on baselines, because in most cases quantitative data are not collected until long after the resource has been modified. This is particularly true for marine communities which can be difficult and expensive to monitor.

A new paper in Coral Reefs “Assessing loss of coral cover on Australia’s Great Barrier Reef over two decades, with implications for longer-term trends” (Sweatman et al. 2011) tries to get at what the baseline is for the Great Barrier Reef (GBR) using the results of ecological surveys performed by the Australian Institute of Marine Science (AIMS). Sweatman et al argue that the AIMS surveys, which began in 1986, are the most reliable evidence we have and that other evidence should be ignored. However, many other scientists surveyed reefs on the GBR (for various reasons) decades before AIMS began it’s monitoring program. Three papers have collated that data and combined it with the AIMS survey data to estimate how the GBR has changed over the last 4-5 decades.

The first such paper (published in Nature by Bellwood et al 2004) included this graphic of long-term change in coral cover (the percentage of the sea floor covered by living corals – because corals facilitate so many reef inhabitants, living coral cover is a key measure of reef habitat quality and quantity, analogous to the coverage of trees as a measure of tropical forest loss):

Figure 1 (from Bellwood et al 2004). Degradation of coral reefs. a, Results of a meta-analysis of the literature, showing a decline in coral cover on the Great Barrier Reef. Each point represents the mean cover of up to 241 reefs sampled in each year. b, The recorded number of reefs on the Great Barrier Reef, Australia, substantially damaged over the past 40 yr by outbreaks of crown-of-thorns starfish (COTS) and episodes of coral bleaching.

The second study (Bruno and Selig 2007) is a meta-analyses of coral reef survey data from 2667 reefs across the Indo-Pacific performed between 1968 and 2004 (Fig. 2).

Figure 2 (from Bruno and Selig 2007). Coral cover in ten Indo-Pacific subregions in each of three periods. Plotted values are means +/- 1 SE and values above each bar are the subregional sample sizes. *=no data available

The third paper, Pandolfi et al 2003, used a variety of historical and palontological data sources in an attempt to reconstruct the longer-term, including pre-human, history of the GBR and other reefs around the world (Fig. 3).

Figure 3 (from Pandolfi 2003). Time trajectories for reef regions over seven cultural periods.

All three studies essentially concluded that GBR coral cover and overall ecosystem health began to decline decades ago, despite the fact that the GBR is currently in better shape than many of the world’s reefs.

Sweatman et al dismiss pre-1986 data from all three studies, arguing that only AIMS survey data are suitable, and thus conclude that the GBR has changed little if at all due to human influences: “We argue that the GBR is currently less degraded from its natural, resilient state than some published reports have asserted”. Global climate change skeptics have frequently use a very similar approach: they rationalize cherry picking a favored data set and time interval in an attempt to show land and ocean temperatures haven’t increased, that sea ice hasn’t declined, etc.

Abstract (from Sweatman et al 2011):

While coral reefs in many parts of the world are in decline as a direct consequence of human pressures, Australia’s Great Barrier Reef (GBR) is unusual in that direct human pressures are low and the entire system of 2,900 reefs has been managed as a marine park since the 1980s. In spite of these advantages, standard annual surveys of a large number of reefs showed that from 1986 to 2004, average live coral cover across the GBR declined from 28 to 22%. This overall decline was mainly due to large losses in six (21%) of 29 subregions. Declines in live coral cover on reefs in two inshore subregions coincided with thermal bleaching in 1998, while declines in four mid-self subregions were due to outbreaks of predatory starfish. Otherwise, living coral cover increased in one subregion (3%) and 22 subregions (76%) showed no substantial change. Reefs in the great majority of subregions showed cycles of decline and recovery over the survey period, but with little synchrony among subregions. Two previous studies examined long-term changes in live coral cover on GBR reefs using meta-analyses including historical data from before the mid-1980s. Both found greater rates of loss of coral and recorded a marked decrease in living coral cover on the GBR in 1986, coinciding exactly with thestart of large-scale monitoring. We argue that much of the apparent long-term decrease results from combining data from selective, sparse, small-scale studies before 1986 with data from both small-scale studies and large-scale monitoring surveys after that date. The GBR has clearly been changed by human activities and live coral cover has declined overall, but losses of coral in the past 40–50 years have probably been overestimated.

For several reasons listed below, I think the main conclusion of Sweatman et al is unsupported once you consider the scientific record as a whole.

1) There is much more pre-1986 data available than Sweatman et al suggest

Our study alone (Bruno and Selig) includes data from 154 surveys of reefs across the Indo Pacific performed between just 1980 and 1982. We found that mean coral cover was 42.5% (95% CI, 39.3 and 45.6). Our analysis includes 104 GBR surveys performed between 1968 and 1983, all from published literature (see Fig. 2).

2) Baseline data from other regions indicates that historically GBR coral cover was higher than it is today (or was in 1986)

In the Caribbean a small number (a few dozen) of reliable quantitative surveys from before the early 1980s suggest the regional mean for coral cover was 30-40% (Gardner et al 2003, Schutte et al 2010: see Figs. 5 and 6 below). Because countless well trained reef scientists were working throughout the region and observed the state of reefs over the last 100 years, most Caribbean reef scientists think that historically, the regional mean of Caribbean coral cover was higher than this; probably closer to 50% (or greater). Most Caribbean reefs of this era were dominated by Acropora spp., as can be seen in the photo below from 1974:

Sweatman et al are effectively arguing that the GBR has naturally lower coral cover (averaging a mere 28%) than the Caribbean, which lacks plating species; even in dense thickets of branching Acroporids (as seen above), Caribbean coral cover rarely exceeds 70% whereas on the GBR, cover can easily reach 100% (see the photo below).

We also have substantially more older survey data for several non-GBR Pacific regions than are available for the GBR. For example, Gomez et al surveyed more than 600 sites in the Philippines in 1981 (Gomez et al 1981). Their work clearly shows a coral baseline far higher than today in the Philippines, the GBR or anywhere else in the world. Also see Fig. 4 below from Bruno and Selig (2010) that suggests the values reported in Gomez et al are representative of other regions at the time. And note the striking difference in the distribution of coral cover values among reefs between the early 1980s and for more recent surveys. Does it look like the Indo-Pacific as a whole, the Philippines or the reefs off mainland Asia haven’t changed? NO! They clearly have. Even assuming we had no pre-1986 coral cover data for the GBR, I don’t think it is logical to assume that the GBR hasn’t followed these global trends and that it has a much lower coral cover baseline than the rest of the world.

Figure 4. (From Bruno and Selig 2007) Histograms illustrating percent coral cover in the Indo-Pacific and selected subregions during different periods.

3) The GBR was already disturbed and changing by the time the AIMS monitoring program began

AIMS began surveying a few dozen reefs along the GBR in 1986 after it became obvious that the reef ecosystem was changing due to over-fishing, sediment pollution from coastal development, ocean warming and predator outbreaks. Sweatman et al argue the values recorded by the early AIMS LTMP surveys of the late-1980s, when cover was roughly 30%, are representative of the pre-human, historical baseline.  I see no reason to assume this given the well-documented anthropogenic disturbances that were already affecting the reef by then (see Fig 1).

4) Nearshore reefs were smothered by sediment from coastal development a century ago

Sweatman et al: Observations and models of the dynamics of flood plumes (Devlin et al. 2001) show that it is the inshore reefs that are frequently exposed to runoff, but these reefs constitute less than 5% of the reef area of the GBR.

Sweatman et al cite the early work of Devlin et al (2001), suggesting that only the inshore reefs are ‘frequently’ exposed to runoff, but this isn’t the case. More recent evidence from CSIRO suggests that terrestrial runoff affects a much greater area of the GBR than Sweatman et al suggest:

The remotely sensed images, taken from February 9 to 13 this year, challenge conventional thought that sediment travelling from our river systems into the GBR is captured by the longshore current and travels no more than 10 to 15km offshore, affecting only the inner Great Barrier Reef Lagoon and the inner reef corals.

Images captured by CSIRO show large plumes of terrestrial material following unconventional patterns and travelling quite fast as far as 65 to 130km, to the outer reef and, in some instances, travelling along the outer reef and re-entering the reef.

Sediment, brown and green against the blues that show 'normal' reef waters, from the Annie River (1), North Kennedy River (2), Normanby River (3) and Marrett River (4) washes into Princess Charlotte Bay, past Flinders Island (5) and along Corbett Reef (6) before being carried into the Fairway Channel (7) and into the ocean. (Credit: CSIRO: GeoScience Australia)

To quote CSIRO scientist Arnold Dekker: “A re-think is needed now that we know where flood plumes go, and what this means as organic micropollutants may be travelling to parts of the reef scientists hadn’t thought to look before”. This suggests that both mid and outer shelf reefs are impacted periodically by flood disturbance – traveling as far as 65-135km, and affecting much more than the 5% that Sweatman et al claim. Why is this important? Scientists from AIMS have already implicated nutrient runoff and and crown of thorns starfish plagues, suggesting that “frequent A. planci outbreaks on the GBR may indeed be a result of increased nutrient delivery from the land”. Further research by Jupiter et al from from the southern GBR shows that whilst the inshore reefs that are exposed to chronic high-magnitude events are clearly degraded, near shore reefs influenced by episodic, high-magnitude exposure are also showing signs of stress, with persistent high cover of fleshy macroalgae. While Sweatman et al select (cherrypick?) the stories that makes the GBR look resilient:

“There is other evidence of recovery; 6 years after bleaching, survey sites on inshore reefs in the Innisfail sector had the highest densities of juvenile corals (<10 cm diameter) of any inshore reefs of the GBR (Sweatman et al. 2007), though the densities of juvenile corals were much lower on inshore reefs in the Townsville sector.”

The inclusion of such data largely glosses over some of the other studies Sweatman et al have co-authored, showing reduced resilience and phase shifts from coral to macroalgal dominance: “In this study, 11 years of field surveys recorded the development of the most persistent coral–macroalgal phase shift (>7 years) yet observed on Australia’s Great Barrier Reef (GBR)” (read more)

5) The early GBR survey data are sound

Sweatman et al: Another concern is that the objectives of many early reef studies predisposed them to select areas of high coral cover…This change in research emphasis is likely to be reflected in the choice of study sites, with early studies selecting sites for their diverse communities and high coral cover where the study organisms are abundant and large samples can be found in a small area.

I initially thought this too, but once I got into the literature, I was reminded that the late 60s and early 70s were the heyday of disturbance ecology and most reef ecologists were community ecologists, and like their peers working in other systems, focused almost entirely on the effects of large disturbances on reef communities, e.g., Endean and Stablum 1973, Endean 1977, Connell 1978, Done 1992, Done et al. 1991, etc.  Thus, if anything, I think most the early bias is in the other direction.  Regardless, I agree site selection biases, both then and now, complicate long-term trend interpretation.

Sweatman et al: While the AIMS long-term data show a decline in average coral cover on GBR reefs from 28.1 to 21.7% between 1986 and 2004, two studies (Bellwood et al. 2004; Bruno and Selig 2007) based on unweighted meta-analyses have suggested that average coral cover on GBR reefs was considerably higher in the 1960s and 1970s than in the 1980s. Bellwood et al. (2004) presented a plot of mean coral cover on the GBR indicating that cover halved from ~40% in the early 1960s to ~20% in 2000, almost three times the rate of decline in the AIMS long-term monitoring data.

Bruno and Selig (2007) used information from 2,667 sites to assess change across the Indo-Pacific, including the GBR as one subregion. Based on published studies including AIMS monitoring data, they found that mean coral cover on the GBR declined by ~25% (in relative terms) from the period 1968–1983 to 1984–1996 and then was relatively stable until the end of their study period in 2004. We argue that this difference is substantially due to a change in the scale of surveys and in survey methods. The most compelling evidence for this is that, in the data sets of both studies, the annual estimates of the mean for coral cover on the GBR drop abruptly in 1986, the first year of large-scale moni- toring on the GBR, and then vary rather little around the new level in subsequent years.

The apparent abrupt drop in average coral cover on the GBR in 1986 is most probably due to the inclusion of AIMS monitoring data with cover estimates from small selected patches of reef from small-scale studies…

Like Sweatmean et al, Bruno and Selig and Bellwood et al found that at a regional scale, average coral cover on the GBR has changed little since 1984 (see Figs. 1 and 2 above).  A similar pattern has been documented for the Caribbean, where substantial coral loss in the early 1980s changed to relative regional stasis since (Figs. 5A and C), i.e., a very similar pattern has been found in other regions (regardless of the scale of surveys and survey methods – also see Bruno and Selig for other Indo-Pacific examples) in which AIMS has never surveyed. 

Figure 5 (From Schutte et al 2010). Annual cover values (±1 SE, closed circles, left y-axis) and site sample sizes (open circles, right y-axis) for (A) mean coral cover for all sites in the Caribbean basin (n = 1962; star: 1980, the year in which Hurricane Allen struck and white band disease outbreaks began); (B) mean macroalgal cover for all sites for which data were available (n = 875; star: 1983, the year in which the Diadema antillarum die-off began); (C) mean coral cover for all sites in the greater Caribbean except those in the Florida Keys (FLK; n = 1515); and (D) mean coral cover for all sites in the FLK subregion (n = 447)

6) Are the AIMS LTMP data sound?

Here’s what Professor Mike Risk had to say about the AIMS monitoring program:

“One of the largest monitoring programmes is operated by the Australian Institute of Marine Sciences (AIMS) (e.g. Sweatman et al. 1998). Like all large monitoring programmes, it is expensive and time-consuming. It is designed to detect changes over time in reef communities at a regional scale. There has been a massive amount of data collected in this programme, which is commendable. On the other hand, as annual surveys are run between September and May, beginning in the north and working south, seasonal changes will be difficult to separate from spatial and temporal changes. It will take perhaps 30-50 years to accumulate enough baseline data to allow useful generalizations to be made” – (Risk 1999)

The AIMS survey data presented in Sweatman et al used the “manta tow” technique; snorkelers are towed behind a boat, over a reef and visually estimate coral cover within 10m wide swaths to categories such as 0-5%, >5-10%, 10-20%, 20-30%, etc. I think the manta technique can be a valid tool for estimating crude spatio-temporal trends in coral cover. I even used the AIMS manta data in our Bruno and Selig paper, although I haven’t used it since (having spoken with several former AIMS technicians about the technique and it’s accuracy and precision). In short, Sweatman et al argue that their manta tow data is so superior to data from other sources, that only the AIMS manta data should be used to asses long-term trends in GBR state. I disagree; not to knock the AIMS manta data, but it is a visual quasi-quantitative estimate collected by technicians as compared to the pre-1986 GBR data which was all collected by renouned PhD scientists, e.g., Endean and Stablum, Connell, Done, etc, that spent their lives studying the GBR.

Furthermore, these pre-1986 GBR surveys were performed using wholly quantitative techniques such as underwater photography to estimate coral cover. I just don’t buy the argument that the AIMS-intern-manta tow data are superior to quantitative surveys by trained PhD scientists. For one, how can we know that the visual estimation of “20%” coral cover has stayed constant over time? Secondly, I really doubt any technique only capable of estimating coral cover to the nearest 10% (i.e., with such low precision) is sensitive enough to even detect the gradual decline in coral cover that has been reported for the GBR and elsewhere, e.g., ~0.5-2% a year. (Just take a look at the error bars in Fig. 2 from Sweatman et al in the Abstract above). Third, I doubt the AIMS manta surveys were run long enough to detect regional trends without including data from other sources. Given the inherent noise in the system, I usually look for 30+ years of data before I try to test for a large-scale trend.

Fourth, I think it is somewhat misleading to represent the manta tows as having far greater spatial coverage. This is only true if you compare the cumulative area of the samples. However, unlike the manta tows, quantitative benthic reef surveys include extensive independent replication and if properly designed will produce coverage estimates that are representative of the broader surrounding benthos.

Finally, I suspect that the manta technique substantially underestimates coral cover because it does not (and cannot) correct for uninhabitable (by corals) substrate that is encountered in surveying. When coral scientists use the term “coral cover”, they mean the percentage of the sea floor occupied by stony corals that is habitable by this group, i.e., hard substrate, not sand or other types of soft substrate. This is easy to factor out with other quantitative survey methods; you just divide the total coral cover by the total hard (suitable) substrate cover to calculate “coral cover”.   In most cases, the hard/suitable cover is nearly 100%. But because manta tows cover wide and long swaths of reef, they inevitably include small and large patches of sand, etc, and it is impossible to do the mental math to factor this out when estimating the coverage of corals and other benthic taxa while getting pulled behind a boat in shark infested waters!  (manta towing is a job for the young and immortal!) If you compare the AIMS manta data to the quantitative AIMS video transect data (~48 reefs surveyed annually) you can see this artifact: from 1994-2003 the mean coral cover from the AIMS manta tows was 21.7 +/- 0.5 (1 se) and 30.7 +/- 0.9 from the video transects. This suggests that the drop in GBR coral cover in the mid-1980s could be due to a methodological bias of the manta tow technique. Would this mean that the GBR hasn’t lost any coral or that “losses of coral in the past 40–50 years have probably been overestimated”?  Only if you think that the coral cover baseline, unlike the rest of the world, for the GBR is only ~30%: as I explained above, I think this is unlikely.

Figure 6 (From Gardner et al 2003). Absolute percent coral cover from 1977 to 2001. Annual coral cover estimates (black triangles) are weighted means with 95% bootstrap confidence intervals. Also shown are unweighted mean coral cover estimates for each year (black circles), the unweighted mean coral cover with the Florida Keys Coral Monitoring Project (1996–2001) omitted (X), and the sample size (number of studies) for each year (white circles, right y axis).

7) Other skeptic soundbites

Sweatman et al make a lot of noise about variation among reefs and subregions in coral cover trajectories and states. Basically, there is a high degree of spatio-temporal asynchrony in the system, as we discussed in Bruno and Selig and illustrated with this graphic:

Figure 7 (from Bruno and Selig 2007). Illustrative examples of asynchrony of coral cover among 25 randomly selected monitored reefs on the GBR (a) and in Indonesia (b).

This isn’t surprising or atypical and it doesn’t mean a long-term trend isn’t present or detectable, as Sweatman et al suggest. Climate change deniers use this argument frequently, suggesting that natural short term variation makes long-term, anthropogenically forced trends, unlikely or undetectable. This is in a sense what Sweatman et al are arguing as well. But the fact that there is great unforced spatiotemporal variation, i.e, noise or weather, does not mean that longer-term, human-induced change isn’t also happening. (Although this is indeed a big issue for many fields of global change science: how to detect slow, long-term trends in a sea of shorter term noise.)

Sweatman et al: A reef system that is stable in the long term will still show cycles of disturbance and recovery at a subregional scale

True, but so will a reef system that isn’t stable and is declining as has been shown for other regions such as the Caribbean (Schutte et al 2010).

Sweatman et al: In the kind of broad analysis presented here, reef resilience is manifested as substantial increases in coral cover following disturbance. In the great majority of sub- regions of the GBR, reefs showed both declines and sub- stantial periods of increasing living coral cover over the 19 years of surveys, evidence that many reefs retained their regenerative capacity.

This, I largely agree with. In fact, there isn’t much doubt that reefs on the GBR have not lost all their regenerative capacity, eg, see here.

Shifting baseline syndrome

In his classic 1995 paper in Trends in Ecology and Evolution, Daniel Pauly outlined his argument for shifting baseline syndrome in fisheries:

Essentially, this syndrome has arisen because each generation of fisheries scientists accepts as a baseline the stock size and species compostion that occurred at the beginning of their careers, and uses this to evaluate changes. When the next generation starts its career, the stocks have further declined, but it is the stocks at that time that serve as a new baseline. The result obviously is a gradual shift of the baseline, a gradual accommodation of the creeping disappearance of resource species, and inappropriate reference points for evaluating economic losses resulting from overfishing, or for identifying targets for rehabilitation measures.

The Sweatman et al paper is a great example of shifting baseline syndrome: coral reef scientists that accept as a baseline the state and coral reef cover that occurred at the beginning of their careers and use this to evaluate changes regardless of valid evidence of previously higher estimates.

In conclusion: The science certainly isn’t settled and I welcome this and future contributions by Sweatman et al and others on the matter.  I started working on this problem about 7 years ago and I frequently ask more experienced scientists and old-timers what they remember from the 60s and 70s and what they think the baseline distribution for coral cover  – which certainly varies among regions – really is.

We can’t know for sure without a time machine. But based on all the data at hand, I feel confident the GBR historically (before people starting mucking it up) had at least twice the coral it has now (including the nearshore reefs that we have lost and don’t even bother to survey anymore). This is pretty much what the vast amount of data (10,000+ surveys) for reefs around the world indicates has happened globally.

In Australia, this topic matters a lot because there has been an ongoing argument about how much the GBR has changed and how threatened it really is.  Sadly, much of this is playing out in the dodgy Aussie newspaper, the Australian. See past debunking of this nonsense about the GBR being “blue again” here, here, here, here and here.

Both shifting baseline syndrome and data cherry picking are more common in hard science and the peer-reviewed literature that you’d think. I am working on a followup post about another case of coral reef scientists playing fast and loose with the data in an attempt to support a pet idea; in this case they exclude a different set of survey data in an attempt to make the opposite point Sweatman et al did, namely to argue that reef decline is worse than has been reported. So stay tuned…

Some background and disclaimers: The lead author, Hugh Sweatman is a colleague and collaborator of mine. We have published several papers together and are working on other collaborative projects and started corresponding about coral reef baselines about five years ago. Dr. Sweatman is the director of the long-term monitoring program at AIMS (the analysis was based on the dataset from this program). I was a reviewer of the manuscript and made the same points in my signed (non-anonymous) review that I made above. Finally, Sweatman et al (2010) directly criticized findings of a paper on which I was the lead author (Bruno and Selig 2007).


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Endean R. (1977). Acanthaster planci infestations of reefs of the Great Barrier Reef. Third International Coral Reef Symposium, 185-191

Endean R. & Stablum W. (1973). The apparent extent of recovery of reefs of Australia’s Great Barrier Reef devastated by the crown-of-thorns starfish. Atoll Research Bulletin, 168, 1-41

Done T. (1992). Constancy and change in some Great Barrier Reef coral communities: 1980-1990. American Zoologist, 32, 655-662

Done T.J., Dayton, P.K.,  Dayton, A.E.,  Stege, R. (1991). Regional and local variability in recovery of shallow coral communities:  Moorea, French Polynesia and central Great Barrier Reef. Coral Reefs, 9, 183-192

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Pesticide impacts on the Great Barrier Reef – Croplife misinformation?

By Jon Brodie.

The pesticide industry group Croplife have recently published their latest assessment of the threat to the Great Barrier Reef from pesticide use. The report can be found at: Barrier Reef. pdf

The report is notable for its extreme ‘cherry picking’ of data with which to make the assessment. It uses one data set from a summary report (not the original science report) for the GBRMPA Marine Monitoring Program from 2007/2008 (Prange et al Reef Water Quality Protection Plan Marine Monitoring Program: 2007/2008 Summary Report pp18-19). Note the Croplife report was very recently released in 2010. The data used is from the use of passive samplers only which are generally deployed only in non-flood conditions and represents the ‘low’ concentration end of pesticide detections in contrast to samples taken in the wet season which are generally much higher (as you might expect).

Since 2007 a large number of pesticide studies in the GBR have occurred and the results have been published in the peer reviewed literature (journals) e.g. Lewis et al 2009; Davis et al 2008; Shaw et al 2010 in marine waters. River discharge of pesticide studies include Packett et al 2009, Lewis et al 2009; Bainbridge et al 2009. Peer reviewed technical reports are also numerous in this period and are all available on the web. Even before 2007 a number of pesticide papers were published with data from rivers and/or marine waters of the GBR e.g. McMahon et al 2005; Shaw and Mueller 2005; Mitchell et al 2005. Finally a considerable body of work on the toxicity of pesticides to GBR organisms (mainly recently from Andrew Negri’s group at AIMS) has been published in the peer reviewed literature since 2007 (and a lot before 2007 as well). If any other readers want access to any of this literature please contact me.

Croplife chose to ignore all this published information and data. When this data is taken into account the outcome is an entirely different assessment, opposite in conclusions to that presented by Croplife.

One wonders at the ethics of a ‘respectable’ industry organisation like Croplife putting out such misleading information. It’s also sad in a period when we are making progress in pesticide management in the GBR catchment with farmers investing in better application technology such as shielded sprayers (see photo) with the assistance of the Australian Government’s Reef Rescue initiative.